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Revista de Biología Tropical, ISSN: 2215-2075, Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

Comparison of fish assemblages recorded by visual census and video census

Luis Gibran Juárez-Hernández1*; https://orcid.org/0000-0003-0658-6818

María Guadalupe Sánchez-Vega1; https://orcid.org/0000-0003-2852-9283

1. Centro Universitario Ciencia e Innovacción para la Formación y el Emprendimiento (CIFE). Calle Tabachín 514,

Bellavista, 62140 Cuernavaca, Morelos, México; gibbjuarez@gmail.com (Correspondence*),

lupitasanchez110406@gmail.com

Received 04-V-2022. Corrected 05-VIII-2022. Accepted 08-VIII-2022.

ABSTRACT

Introduction: Underwater visual censuses are the basis of many studies on fish ecology, however, a series of

limitations and errors influence the traditional visual estimation of fish richness and abundance. Video tech-

niques have been proposed to mitigate such errors, but there are few studies that compare the effectiveness of

both methods.

Objective: To compare the estimates obtained through the traditional census and the video census of the fish

community of two localities in the central Mexican Pacific.

Methods: We studied the fish community of two bays of Huatulco, Oaxaca, Mexico. We established sampling

points in each bay and applied a traditional census and a diver-operated video census. We used comparison tests

and analysis of similarity tests to compare richness, abundance and diversity by locality; and permutation tests

for the same parameters at each sampling point.

Results: Both censuses provide similar estimates regarding the richness, abundance, and diversity by locality

and by sampling points. There were no statistically significant differences between traditional census and a diver-

operated video census in terms of richness, abundance, and diversity.

Conclusions: Video census using the diver-operated video technique can be used as a complement or as an

alternative to traditional census. Its use can provide a more complete assessment, increase data acquisition,

and implement long-term monitoring programs in areas where there are economic limitations for its operation.

Key words: sampling methods; Maguey; Huatulco; ichthyofauna; Mexican Pacific.

https://doi.org/10.15517/rev.biol.trop.2022.48420

AQUATIC ECOLOGY

The underwater visual census forms the

basis of many studies on the ecology of fish in

fresh and marine shallow waters (Caldwell et

al., 2016; Samoilys & Carlos 2000). Since its

implementation in the 1950s, it has become the

preferred method for sampling reef fish com-

munities (Kulbicki et al., 2010; Pais & Cabral,

2017; Thanopoulou et al., 2018), as a result

of it being a non-destructive (Thanopoulou et

al., 2018; Widmer et al., 2019; Yulianto et al.,

2015) and inexpensive method (Holmes et al.,

2013; Watson & Quinn, 1997) that offers quick

estimates of the richness, the abundance, and

the sizes of fish (Samoilys & Carlos, 2000).

Although its use has spread, it is impor-

tant to note that it presents limitations for

its execution, related to environmental fac-

tors (depth, water clarity, weather conditions),

logistics (immersion time or sampling fre-

quency) (Emslie et al., 2018; Holmes et al.,

2013; Williams et al., 2006), influence of

the diver on the behavior of certain species

542 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

(attraction or repulsion) (Dickens et al., 2011;

Pais & Cabral, 2017; Pereira et al., 2016) and

error pathways, being these related to the diver

(experience, ability, and behavior) (Assis et al.,

2013; Bozec et al., 2011; Widmer et al., 2019),

erroneous identification of the species, under-

estimating the abundance of small and cryptic

species (Willis, 2001) and overestimating the

most abundant (Williams et al., 2006), which

influence the estimation of the richness and

abundance (Brock, 1982; García-Charton et

al., 2000) and therefore may compromise the

ability to detect significant changes in the fish

community (Langlois et al., 2010; Wakefield

et al., 2013).

Regarding the afore mentioned, the imple-

mentation of techniques based on video has

been proposed (Langlois et al., 2010; Mallet &

Pelletier, 2014). Although the development of

video sampling methodologies for the study of

marine communities dates back to the 1950s,

there were several limitations (cost and low

operation of the equipment, battery autonomy,

storage capacity) (Bacheler et al., 2017; Wid-

mer et al., 2019), these have been overcome as

a result of technological progress (greater oper-

ability, autonomy and capacity) and that are

economically more affordable (Goetze et al.,

2019; Mallet & Pelletier, 2014; Zarco-Perello

& Enríquez, 2019).

With regards to its advantages, it is speci-

fied that they allow to reduce the error related

to the variability between observers, since the

information can be verified (Assis, 2013; Lan-

glois et al., 2010; Widmer et al., 2019). It´s a

permanent record, it allows to re-examine the

data for various purposes (Goetze et al., 2019;

Pelletier et al., 2011; Tessier et al., 2013), and

it allows to collect field data by divers who are

not experts in fish identification (Pelletier et al.,

2011; Tessier et al., 2005; Tessier et al., 2013).

Operationally, among its disadvantages are

the cost of the equipment, complications for its

execution (Holmes et al., 2013; Widmer et al.,

2019), the precision with respect to the human

eye (Bortone et al., 2000; Holmes et al., 2013;

Tessier et al., 2005), as well as the limitation

to identify small and cryptic species (Goetze

et al., 2019; Grane-Feliu et al., 2019; Wilson

et al., 2018). Other aspects that have been

mentioned are that it can be more expensive

and slower than the traditional census since it

involves video processing for analysis (Grane-

Feliu et al., 2019; de la Guardia et al., 2021;

Holmes et al., 2013).

Within the video method, the most recog-

nized techniques are stationary (with bait or

without bait), diver-operated video (DOV), and

remote underwater video (Mallet & Pelletier,

2014; Schramm et al., 2020; Wilson et al.,

2018). According to Murphy & Jenkins (2010)

as well as Goetze et al. (2015) report that each

technique offers advantages and disadvantages.

Of these techniques, those operated by divers

(DOV) stand out, since they are considered the

most profitable for estimating the abundance

and richness of fish communities (Goetze et al.,

2015; Grane-Feliu et al., 2019; Langlois et al.,

2010; Wilson et al., 2018). Watson et al. (2005)

refers that this technique allows greater maneu-

verability of the camera(s), which offers advan-

tages in structurally complex habitats such as

coral reefs. Likewise, it is specified that this

technique is the most pertinent when there is

an interest in the associations of fish with a par-

ticular type of habitat or physical structure due

to the ability to restrict the size of the sample

unit (Galaiduk et al., 2017; Tessier et al., 2013).

This technique consists in the use of a

video camera(s) to record the route that is made

in the sampling unit, the identification of the

species and registration of their abundance is

carried out later by viewing the recording on a

computer monitor (Goetze et al., 2015). Within

the DOV, two variations are recognized, the first

is the use of a single camera where the tech-

nique consists of the video operator swimming

alongside the diver who performs the census

(Bortone et al., 1991; Pelletier et al., 2011; Tes-

sier et al., 2005), and the second consists of a

system where two cameras are mounted on a

base (stereo video) (S-DOV) and in the same

way the video operator swims next to the diver

who performs the census (Goetze et al., 2015;

Harvey et al., 2001; Harvey et al., 2004; Lan-

glois et al., 2010).

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Taking them into account, studies that

have compared the traditional census with the

S-DOV are frequent (Grane-Feliu et al., 2019;

de la Guardia et al., 2021; Wilson et al., 2018),

this is not the case for studies that compare the

DOV with the traditional one (Bortone et al.,

1991; Tessier et al., 2005; Tessier et al., 2013;

Wartenberg & Booth, 2015). These studies

coincide that through both methods they can

provide comparable estimates, however, it is

emphasized that a greater number of species

and individuals are recorded through the tradi-

tional census.

In this regard, it should be noted that the

implementation of the diver-operated video

technique to evaluate ichthyofauna in the Mexi-

can Pacific is limited, and there is no informa-

tion on its use. Therefore, the present objective

is to compare the estimates obtained through

the traditional census and the video census of

the fish community of two localities in the cen-

tral Mexican Pacific.

MATERIALS AND METHODS

Study area: The localities selected to

carry out the study were Maguey and La

Entrega bays, which are located in the complex

“Huatulco Bays” (15°40’48” - 15°45’36” N

& 96°14’24” - 96°07’13” W), on the coast

of the state of Oaxaca, Mexico (Fig. 1). This

area is considered one of the most important

regions in the reef ecosystems of the Mexican

Pacific, since it is home to a great diversity

of species of echinoderms, corals, and fishes

(Juárez-Hernández & Tapia-García 2017;

Juárez-Hernández & Tapia-García, 2018a;

López-Pérez et al., 2014). Both bays are char-

acterized by high species richness, abundance,

Fig. 1. Location of the study area “Huatulco Bays”. Distribution of sampling points in A. Maguey Bay and B. La Entrega

Bay.

544 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

and fish diversity (Juárez-Hernández & Tapia-

García, 2017; Juárez-Hernández et al., 2021;

López-Pérez et al., 2010).

Sampling strategy: The sampling was

carried out in September 2019, and the selec-

tion of the sampling sites in each locality corre-

sponded to previous studies (Juárez-Hernández

& Tapia-García, 2017; Juárez-Hernández et al.,

2021). Specifically for Maguey, nine sampling

points were selected and eight for La Entrega.

These points covered environments with rocky

substrate (M1, E1), coral (M7, E3, E4, E5; E6,

E7), coral rubble (E8), sand (M4, M5) as well

as mixed environments, such as coral-rocky

(M3, M8), rocky-coral (M2, M9) and sandy-

rocky-mixed (M6) (Fig. 1). The depth at these

sampling points was at least 3 m and the maxi-

mum was 10 m.

At each sampling point, a 10 meter long

transect was established, in which the tradi-

tional census (TC) and the video census (VC)

were carried out using the diver-operated video

technique (DOV) by the same subject using

free diving (snorkel) (Fig. 2). Therefore, the

video camera was placed in the visor of the

observer, which is designed for this purpose.

The equipment used to record was a Mobo

action camera, model 9031 and the camera

parameters were 4K recording (Ultra High

Definition- 3840x2160) without any zoom. It

is required that the observer be trained in the

identification of the fish species and the execu-

tion of the method.

The procedure consisted of the observer

standing at one end of the transect, recording

the transect number on an acrylic table, and

then turning on the camera and recording the

transect number annotation. In this way, the

recording began as the observer recorded the

species and their abundance on the acrylic

table. In each transect three routes were made,

10 meters each (Fig. 2), the first was to the

opposite end of the transect (near the surface)

(Fig. 2A), then back to the point of origin (mid-

water) (Fig. 2B), and finally a third route to the

opposite end of the transect (near the bottom)

(Fig. 2C). At the end of the routes, both the

recording of fish in the acrylic table, as well

as the recording, stopped. The duration of the

routes was approximately five minutes.

The videos were viewed two months after

sampling on a 23-inch monitor. The analysis of

the video was similar to the in-situ procedure

carried out in the traditional census, that is, at

the beginning of the video the species and num-

ber of individuals were recorded on a sheet of

paper. It is specified that the video was played

continuously and without pauses, for a total of

five minutes.

Fig. 2. Representation of the routes made at each sampling point. A. near the surface, B. mid-water and C. near the bottom.

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Data analysis: The taxonomic status of

the species was verified according to Fricke et

al. (2020a) and the taxonomic arrangement was

based on Fricke et al. (2020b). For each of the

censuses (TC and VC), on each sampling point

and locality, the number of species, abundance

(number of individuals), and diversity (Shan-

non & Wiener, 1963) were calculated. Species

accumulation curves were performed using the

non-parametric estimator (Chao 1) based on

abundance. The curves were constructed with

9 000 randomizations using the EstimateS v9

packet (Colwell, 2013).

For each locality, the results of each cen-

sus were compared using a qualitative simi-

larity coefficient (Sorensen). The degree of

agreement between the observations of both

censuses was evaluated by means of Kend-

all’s W concordance coefficient (Kendall &

Smith, 1939; Legendre, 2005). Paired t-tests

were carried out to compare the number of

species, abundance, and diversity by type of

census in each locality, when the normality

assumption was fulfilled (Shapiro-Wilk test,

P > 0.05), and if this assumption was not test-

able, the Wilcoxon test was applied (Whitlock

& Schluter, 2009). To compare the number of

species, abundance, and diversity of the same

sampling site (environment) by type of census,

permutation tests were used. This test calcu-

lates the richness, abundance, and diversity

for two samples and compares each of these

parameters using permutations (9999) (Ham-

mer, 2021). In addition, a meta-analysis was

carried out (Sokal & Rohlf, 1995) considering

the p values of each of these tests with the

objective of verifying if there were differ-

ences in the number of species, abundance and

diversity between census type by locality. For

this analysis it was taken into account that if

the resulting value of the product of the meta-

analysis (-2 Σ Ln P) was greater than the value

of the Chi-square statistic (α = 0.005 with 2*k

degrees of freedom), there were differences

between the attribute analyzed (number of spe-

cies, abundance, diversity) by type of census.

The evaluation of the degree of similarity of the

ichthyofauna between the types of census was

carried out using the Bray-Curtis index (Clarke

& Warwick, 1994), and its analysis was carried

out by a Non-metric Multidimensional Scaling

(nmMDS) and analysis of similarity (ANO-

SIM) (Clarke, 1993) with permutation (9999)

to identify significant differences in terms of

composition and abundance of fish. If the simi-

larity analysis revealed differences, a similarity

percentage analysis (SIMPER) (Clarke, 1993)

was performed to identify the species that con-

tribute to the differentiation between both types

of censuses (TC vs VC). Finally, the abundance

of the most represented species was compared

between both types of censuses (TC vs VC)

using paired t-tests, or, when appropriate, using

the Wilcoxon test. All tests and analyzes were

carried out with the Past V.4.5 packet (Hammer

et al., 2001).

RESULTS

Maguey Bay: In the traditional census

(TC), 27 species (Mean = 7.25 ± 3.32) cor-

responding to 21 genera, 13 families, and

seven orders were identified (Table 1). The

total abundance was 235 individuals (Mean =

9.37 ± 15.68), the diversity was 2.172 (Mean

= 1.41 ± 0.38) (Fig. 3). According to the Chao

1 estimator, the expected number of species

was 33. Stegastes acapulcoensis, Thalassoma

lucasanum and Microspathodon dorsalis were

the most abundant species.

In the video census (VC), 21 species

(Mean = 6.5 ± 2.56) corresponding to 16 gen-

era, 10 families and five orders were identified

(Table 1). The abundance was 203 individuals

(Mean = 24.62 ± 10.62), the diversity was

1.969 (Mean = 1.38 ± 0.42) (Fig. 3). Accord-

ing to the Chao 1 estimator, the expected

number of species was 23. S. acapulcoensis,

T. lucasanum and M. dorsalis were the most

abundant species.

The species that were only identified

using the traditional method were: Arothron

meleagris, Canthigaster punctatissima, Epi-

nephelus labriformis, Fistularia commersonii,

Halichoeres chierchiae, H. nicholsi, Johnran-

dallia nigrirostris, Kyphosus vaigiensis and

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TABLE 1

Taxonomic list of the fish community of Maguey and La Entrega bays

Class Order Family Species Maguey Entrega

TC VC TC VC

Actinopteri Syngnathiformes Fistularidae Fistularia commersonii Rüppell, 1838 1 1 1

Carangiformes Carangidae Caranx caballus Günther, 1868 5 1

Caranx caninus Günther, 1867 2 5

Trachinotus rhodopus Gill, 1863 4 3

Mugiliformes Mugilidae Mugil curema Valenciennes, 1836 7 1

Acanthuriformes Pomacanthidae Holacanthus passer Valenciennes, 1846 3322

Chaetodontidae Chaetodon humeralis Günther, 1860 2

Johnrandallia nigrirostris (Gill, 1862) 1 3 2

Acanthuridae Acanthurus xanthopterus Valenciennes, 1835 2 5

Prionurus laticlavius (Valenciennes, 1846) 11 13 9 14

Tetraodontiformes Tetraodontidae Arothron meleagris (Anonymous, 1798) 1 6 7

Canthigaster punctatissima (Günther, 1870) 1

Ostraciidae Ostracion meleagris (Shaw, 1796) 1

Balistidae Sufflamen verres (Gilbert and Starks, 1904) 1 2

Centrarchiformes Kyphosidae Kyphosus elegans (Peters, 1869) 7 1

Kyphosus vaigiensis (Quoy and Gaimard, 1825) 2 1 2

Cirrhitidae Cirrhitichthys oxycephalus (Bleeker, 1855) 3

Perciformes Serranidae Cephalopholis panamensis (Steindachner, 1877) 3 2

Epinephelus labriformis (Jenyns, 1840) 1 1

Lutjanidae Lutjanus argentiventris (Peters, 1869) 3 2

Mullidae Mulloidichthys dentatus (Gill, 1863) 1 2

Pomacentridae Abudefduf concolor (Gill, 1862) 3 2

Abudefduf troschelii (Gill, 1862) 2 2 3

Azurina atrilobata (Gill, 1862) 10 4

Microspathodon bairdii (Gill, 1862) 1711

Microspathodon dorsalis (Gill, 1862) 24 27 7 11

Stegastes acapulcoensis (Fowler, 1944) 94 81 84 68

Stegastes flavilatus (Gill, 1862) 141

Labridae Bodianus diplotaenia (Gill, 1862) 6443

Halichoeres chierchiae Di Caporiacco, 1948 1

Halichoeres dispilus (Günther, 1864) 2 1

Halichoeres nicholsi (Jordan and Gilbert, 1882) 1 2

Halichoeres notospilus (Günther, 1864) 2 4

Thalassoma lucasanum (Gill, 1862) 43 30 105 96

Scaridae Scarus ghobban Forsskål, 1775 1

Scarus perrico Jordan y Gilbert, 1882 2 5

Species registered in the traditional census (TC) and video census (VC) in in each locality.

Sufflamen verres. For their part, the species

that were only identified by video were Cir-

rhitichthys oxycephalus, Kyphosus elegans and

Stegastes flavilatus. Through the video census,

77 % of the species observed by the traditional

census were recorded.

The species similarity between both meth-

ods was 75 % (Sorensen). The degree of

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agreement between observers was substantial

(W = 0.766, P = 0.029). Number of species (t

= 0.8143, P = 0.4422), abundance (t = 1.1232,

P = 0.2983) and diversity (t = 0.2897, P =

0.7804) did not show differences between the

type of census, as well as by environment (P

> 0.05) According to the meta-analysis, the

number of species (10.80 < 37.2), abundance

(30.80 < 37.2) and diversity (14.10 < 37.2)

showed no differences between census types.

The non-metric scaling showed the similarity

of the ichthyofauna recorded by both censuses

(traditional and video) both by sampling point,

as well as in a general way (Fig. 4A). Regard-

ing composition and abundance, no differences

were found (ANOSIM = -0.078, P = 0.8914).

The abundance of the dominant species did

not show differentiation (S. acapulcoensis: t =

0.759, P = 0.461), (T. lucasanum: t = 0.853, P

= 0.418), (M. dorsalis: W = 13.5, P = 0.092).

La Entrega Bay: In the traditional census

(TC), 20 species (Mean = 6 ± 3.03) belonging

to 16 genera, 12 families, five orders were

identified (Table 1). The total abundance was

239 individuals (Mean = 29.87 ± 12.33), the

diversity was 1.601 (Mean = 1.21 ± 0.486)

(Fig. 2). According to the Chao 1 estimator,

the expected number of species was 23.5. T.

lucasanum, S. acapulcoensis and P. laticlavius

were the most abundant species.

On the other hand, the video census (VC)

identified 18 species (Mean = 5.12 ± 3.39)

belonging to 16 genera, 11 families, five orders

were identified (Table 1). The abundance was

225 individuals (Mean = 28.125 ± 8.166), the

diversity was 1.741 (Mean = 1.13 ± 0.53) (Fig.

2). According to the Chao 1 estimator, the

expected number of species was 19. T. lucasa-

num, S. acapulcoensis and P. laticlavius were

the most abundant species.

The species that were only identified

by the traditional method were Halichoeres

nicholsi, Kyphosus elegans, Microspathodon

bairdii, Ostracion meleagris, Scarus ghob-

ban and Sufflamen verres. The species that

Fig. 3. Variation of the number of species, abundance, and diversity between the traditional census (TC) and video census

(VC) in each locality.

548 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

were only identified through the video census

were Abudefduf troschelii, Chaetodon hume-

ralis, Epinephelus labriformis and Kyphosus

vaigiensis. Through the video, 90 % of the

species observed by the traditional census were

recorded.

The species similarity between both meth-

ods was 78 % (Sorensen). The degree of agree-

ment between observers was very high (W

= 0.803, P = 0.036). Number of species (t =

1.433, P = 0.1949), abundance (W = 22.5, P =

0.5281) and diversity (t = 0.870, P = 0.4129)

did not show differences between the type of

census, as well as by environment (P > 0.05).

The meta-analysis corroborated these results,

as it showed that the number of species (12.86

< 34.26), abundance (22.76 < 34.26) and diver-

sity (14.90 < 34.26) were not different between

census types. Through non-metric scaling,

the similarity of the ichthyofauna recorded

by both censuses (traditional and video) was

observed both by sampling point, as well as in

a general way (Fig. 4B). In the same way, the

composition and abundance did not show dif-

ferences between the type of census (ANOSIM

= -0.05497, P = 0.8197). The abundance of

the dominant species did not show differentia-

tion (T. lucasanum: t = 0.4269, P = 0.682), (S.

acapulcoensis: t = 2.116, P = 0.109), (P. lativ-

lavius: W = 2, P = 0.654).

DISCUSSION

According to the results, it is specified that

the similarity of species between both tech-

niques in each locality was high (more than 70

%), as well as that related to orders, families,

genera, and dominant species. Regarding the

comparison of the composition and structure,

number of species, abundance and diversity

of the fish community and dominant spe-

cies between both methods, no significant

Fig. 4. Non-metric multidimensional scaling of sampling points carried out using the traditional census (solid line) and video

census (punctuated line) in A. Maguey Bay and B. La Entrega Bay.

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differences were found in each locality, which

is different to studies that have used a tech-

nique similar to the one presented here (DOV)

(Pelletier et al., 2011; Tessier et al., 2005;

Tessier et al., 2013), but it is similar to that

reported by Bortone et al. (1991) as well as

Wartenberg & Booth (2015) who used the

same technique, as well as other works that

used the S- DOV (Grane-Feliu et al., 2019; de

la Guardia et al., 2021).

Probably no significant differences will

be found, it is the result of the way in which

the chosen technique (DOV) was implemented

as well as the technique itself, conjoined with

the experience of the observer both in the iden-

tification of the fish, as well as in the execu-

tion of the census (traditional and by video).

Regarding its execution, the observer who

registered the species is the same one who car-

ried out the recording and analysis of it, which

determines that there is a high concordance

between observations, which is different from

the way in which it was carried out in other

works that have used the DOV (Bortone et al.,

1991; Pelletier et al., 2011; Tessier et al., 2005;

Tessier et al., 2013), since they used a second

observer to record the video. Regarding the

chosen technique, compared to other video

techniques, it allows greater maneuverability

of the camera(s), which offers advantages in

structurally complex habitats such as coral

reefs (Watson et al., 2005). This allowed for

an adequate characterization of the fish com-

ponents (surface, mid-water, and bottom), and

of particular of the cryptic fish component, for

which the third route was carried out, which is

recommended to adequately characterize this

component (Holmes et al., 2013; Pelletier et al.,

2011; Watson et al., 2005).

One aspect that was considered to cause

differences in the number of species, abun-

dance and diversity between both techniques

was the complexity of the habitat (determined

by the combination of substrates, number of

coral species, depth, or exposure to waves)

for certain environments, which are charac-

terized by presenting a greater number of

fish species and abundance (Juárez-Hernández

& Tapia-Garcia, 2018a; Juárez-Hernández &

Tapia-Garcia, 2018b; Juárez-Hernández et al.,

2013). Specifically, in Maguey Bay these envi-

ronments are the mixed, coral, and rocky-coral

environments (Juárez-Hernández et al., 2021),

and in La Entrega the coral and rubble-sandy

environments (Juárez-Hernández, 2014), how-

ever, it was found that there were no significant

differences in the community parameters ana-

lyzed in the mentioned environments, as well

as for the rest of the environments.

Given these results, it can be specified that

the DOV technique provides comparable esti-

mates of richness and abundance with respect

to the traditional census, coinciding with that

reported by Bortone et al. (1991) as well as

Wartenberg & Booth (2015), revealing that the

DOV can be considered as a complementary

technique and/or equivalent to the traditional

census (Davis et al., 2014; Wartenberg &

Booth, 2015). Similar conclusions have been

obtained using the S-DOV technique (Grane-

Feliu et al., 2019; de la Guardia et al., 2021;

Wilson et al., 2018).

Considering its complementary character

for Maguey Bay, combining the information

from both techniques provides a total of 29 spe-

cies, this estimate being similar to that obtained

by Juárez-Hernández et al. (2013), in which the

sampling effort was higher (15 transects) than

that carried out here. In La Entrega, when com-

bining the information, it provides a total of

23 species, this estimate being higher than that

obtained in a sampling carried out in Septem-

ber 2010 with the same sampling effort (nine

transects) (Juárez-Hernández, 2014). It should

be noted that both mentioned studies used two

observers and transects of the same length as

the ones used in this study.

In addition to the aforementioned, the use

of this technique as a complement has sev-

eral advantages, one of which is that it offers

a permanent record, allowing the correction

of misidentified in situ species (Bortone et

al., 1991; Langlois et al., 2010; Wartenberg

& Booth, 2015), it limits the potential effects

of the observer, since the video can be viewed

and examined repeatedly by different people

550 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

(Langlois et al., 2010; Pelletier et al., 2011;

Preuss et al., 2009), it provides additional infor-

mation, since the characteristics of the habitat

are recorded on the video (Pelletier et al., 2011;

Tessier et al., 2013; Wilson et al., 2018). This is

essential since many times the observer, being

focused on registering and counting the fish,

is not able to adequately characterize the reef

architecture and the attributes associated with it

(Preuss et al., 2009; Tessier et al., 2013; Wart-

enberg & Booth, 2015).

The disadvantages of video methods have

been stipulated to be the cost associated with

purchasing the equipment as well as the addi-

tional time it takes to process and analyze the

recording (Goetze et al., 2019; de la Guardia

et al., 2021; Tessier et al., 2013). Regarding

the cost of the equipment used for this study,

it is specified that it was low (<$100 dollars),

highlighting the role of action cameras, which

offer a perfect balance among price, image

quality, and operability (Letessier et al., 2015;

Zarco-Perello & Enríquez, 2019), thus granting

viability and accessibility (Goetze et al., 2015;

Letessier et al., 2015). In relation to the proce-

dure, processing and analyzing the recording,

as well as the execution of the census and its

analysis in the study, did not last more than

five minutes and it should be clarified that the

video was not edited so it was viewed exactly

as it was recorded. Whereas these aspects allow

us to consider this technique as profitable,

coinciding with what has been described by

various authors (Grane-Feliu et al., 2019; Lan-

glois et al., 2010; Tessier et al., 2005), it is vital

to mention that a more detailed analysis of the

recording (setting a longer time for its analysis)

would provide valuable additional information.

Considering all these elements, it can

be indicated that the combination of both

techniques could provide a more complete

evaluation and a permanent record of all fish

(Grane-Feliu et al., 2019; de la Guardia et

al., 2021; Wartenberg & Booth, 2015), which

undoubtedly can increase the spatial and

temporal scope of the monitoring programs,

potentially improving the understanding of the

environmental and anthropogenic changes in

fish communities (Wilson et al., 2018). The

foregoing is highly significant in reef systems

given their current situation (Hoegh-Guldberg

et al., 2017; Hughes et al., 2017), since, if

biodiversity is to be conserved, it is necessary

to evaluate it in an adequate and representative

way through a census (Jackson et al., 2001;

Wilson et al., 2018) using an appropriate sur-

vey method (Rotherham et al., 2007; Thomas,

1996; Wartenberg and Booth, 2015).

Although the differences were not signifi-

cant, it is denoted that using of the TC a greater

number of species and abundance were reg-

istered, which is consistent with other studies

that have used the DOV (Bortone et al., 2000;

Pelletier et al., 2011; Tessier et al., 2005), as

well as other video techniques (S-DOV) (Davis

et al., 2014; de la Guardia et al., 2021; Wilson

et al., 2018). The fact that a greater number of

species and abundance is recorded has been

explained under various points, the first of

which is that the field of view of the camera is

smaller than that of the observer (Bortone et al.,

2000; Tessier et al., 2013; Widmer et al., 2019),

that the definition capacity of the human eye is

greater than that of the video camera (Holmes

et al., 2013; Lowry et al., 2012; Wilson et al.,

2018), and that the identification of the species

in a video projected on a screen is more com-

plex because the resolution is lower than that

of the human eye (de la Guardia et al., 2021;

Pelletier et al., 2011). These conditions, at first,

would limit the equivalent character, as referred

by Tessier et al. (2005), however, with techno-

logical advancement and multiple options and

configurations of action cameras (Goetze et

al., 2015; Goetze et al., 2019; Zarco-Perello &

Enríquez, 2019), these limitations can be over-

come, and therefore, their equivalence char-

acter could be established (Grane-Feliu et al.,

2019; de la Guardia et al., 2021; Wartenberg &

Booth, 2015).

Another aspect that has been referred to is

that indicated by Bortone et al. (1991) as well as

by Tessier et al. (2013) who refer that the reason

why a greater number of species are identified

by TC is that unlike the camera, the observer

can turn his head to survey fish. However, with

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the technique used here, since the camera is

attached to the observer’s visor, it rotates in the

direction where the observer’s view is directed.

Although this is an advantage, it must be speci-

fied that in some cases in the present study it

resulted in an inconvenience, since the used

camera does not have an image stabilization

system, determining that when the observer

made “sudden” movements to observe species,

the image is destabilized, limiting the identifi-

cation of the species and the recording of their

abundance. Probably this situation determined

that in Maguey the percentage of species that

were recorded in the video was lower (77 %)

than in the traditional census. This compared to

La Entrega, which through the video recorded

90 % of the species in comparison to the tradi-

tional census. The foregoing refers to the fact

that the environments of Maguey, unlike La

Entrega, are characterized by having a greater

structural complexity, meaning that they pres-

ent a greater number of species and abundance

(Juárez-Hernández, 2014; Juárez-Hernández

& Tapia-García, 2017), which within the sam-

pling determined to carry out a greater number

of movements, causing the loss of stability of

the video and therefore limiting the identifi-

cation of the species. To reduce this effect, it

is necessary to purchase a camera that has an

electronic stabilization system.

Video techniques have been established

to be deficient in identifying small and cryptic

species (de la Guardia et al., 2021; Holmes et

al., 2013; Wilson et al., 2018). In this order,

for Maguey Bay of the eight species not iden-

tified through the video, only three of these

are considered cryptic or associated with the

substrate (Halichoeres chierchiae, H. nicholsi

and Epinephelus labriformis) (Robertson &

Allen, 2015), while for La Entrega, only four

species were not identified through the video

(Table 1), being H. nicholsi the only of these

considered as cryptic. As it can be seen, only

a minimal percentage of the species referred

to as cryptic was not observed through the

video, which may be the result of the technique

used (DOV) and the third route, which is pre-

cisely designed to characterize the cryptic or

components associated to the bottom (Holmes

et al., 2013; Pelletier et al., 2011; Watson et

al., 2005). In accordance with this argument,

it is noted that only with the video the species

Cirrhitichthys oxycephalus was recorded in

Maguey, which has been referred to as cryptic

and small (Juárez-Hernández & Tapia-Garcia,

2018b; Robertson & Allen 2015; Thomson et

al., 2000), while for La Entrega only with the

video were Chaetodon humeralis and Epineph-

elus labriformis registered, both associated

with the substrate (Robertson & Allen, 2015).

Species of other components (Abudefduf tros-

chelii y Kyphosus elegans) (Robertson & Allen,

2015), were only recorded through video and

not through TC, this is the result of the time

allocated by the observer to record the spe-

cies and its abundance in the acrylic, which is

consistent with what was reported by Tessier et

al. (2013), who referred that with a lot of infor-

mation to write at the same time (species and

their abundance), the risk of losing information

increases, therefore the use of audio recording

was recommended instead of performing the

annotations on acrylic (Bortone et al., 1991).

According to this point, the value of the video

recording is denoted, eliminating this problem

(Langlois et al., 2010; Watson et al., 2005; Wat-

son et al., 2010).

An aspect to highlight of the technique

used here that would reveal its high signifi-

cance is that it can be carried out by an

observer who is not an expert in fish identi-

fication (Mallet & Pelletier, 2014; Pelletier et

al., 2011; Wartenberg & Booth, 2015), which

determines that this is a profitable technique,

since it would allow simultaneous studies to

be carried out in different places (Mallet &

Pelletier, 2014; Tessier et al., 2013; Wilson et

al., 2018). In this regard, volunteers have been

posited as a significant source of help in col-

lecting marine biodiversity information, as it is

a cost-effective way to fill spatial and temporal

gaps in traditional monitoring programs (Edgar

et al., 2014; Lamine et al., 2018). Although this

could be feasible, it is necessary to emphasize

that the method must be easy to apply (Lamine

et al., 2018) and that the volunteers must be

552 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 70: 541-556, Enero-Diciembre 2022 (Publicado Ago. 16, 2022)

given training on the characteristics of the sam-

pling, behavior, performance, specifications

on routes and sampling time (Aburto-Oropeza

et al., 2015; Edgar et al., 2014; Lamine et al.,

2018). Therefore, the technique implemented

here could be feasible in these terms, since the

equipment is inexpensive, the method is easy to

apply, and the training would be minimal, How-

ever, it is emphasized that when carried out by

free diving (snorkeling), its implementation

is limited to shallow areas. Considering these

points, the implementation of this technique in

the study area could be functional for the estab-

lishment of long-term monitoring programs

with the help of volunteers (Harvey et al., 2013;

Wilson et al., 2018).

The development of biotic inventories and

the quantification of biodiversity are essential

for the to the development and application of

relevant and successful management and con-

servation strategies (López-Pérez et al., 2013;

Lubchenco & Grorud-Colvert, 2015; Perrings

et al., 2011). Therefore, it is essential to explore

and implement profitable methods and tech-

niques that allow the fulfillment of such objec-

tives in an adequate and representative manner.

According to the above, the technique used

in the present study can be considered under

these characteristics, highlighting the two men-

tioned ways of use, the first being called as a

complement and the second as being called

equivalence that could be of high value. The

technique, being economical and easy to exe-

cute, could be functional in those areas where

the monitoring programs present problems for

their operation resulting from limitations in

their resources (material and human).

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 fol-

lowed all pertinent ethical and legal procedures

and requirements. All financial sources are

fully and clearly stated in the acknowledge-

ments section. A signed document has been

filed in the journal archives.

ACKNOWLEDGMENTS

To the anonymous reviewers for their valu-

able comments and observations.

RESUMEN

Comparación de ensamblajes de peces registrados

por censo visual y censo por video

Introducción: Los censos visuales submarinos son la base

de muchos estudios sobre ecología de peces, sin embargo,

una serie de limitaciones y errores influyen en la estima-

ción visual tradicional de la riqueza y abundancia de peces.

Se han propuesto las técnicas de video para mitigar tales

errores, pero existen pocos estudios que comparen la efec-

tividad de ambos métodos.

Objetivo: Comparar las estimaciones obtenidas mediante

el censo tradicional y el video censo de la comunidad de

peces de dos localidades del Pacífico central mexicano.

Métodos: Se estudió la comunidad de peces de dos bahías

de Huatulco, Oaxaca, México. Se establecieron puntos de

muestreo en cada bahía y se aplicó el censo tradicional

y video censo operado por buzo. Se emplearon pruebas

de comparación y análisis de pruebas de similitud para

comparar riqueza, abundancia y diversidad por localidad;

y pruebas de permutación para los mismos parámetros en

cada punto de muestreo.

Resultados: Ambos censos proporcionan estimaciones

similares en cuanto a la riqueza, abundancia y diversidad

por localidad y por punto de muestreo. No existieron dife-

rencias estadísticamente significativas entre el censo tradi-

cional y video censo operado por buzo respecto a riqueza,

abundancia y diversidad.

Conclusiones: El video censo mediante la técnica de video

operado por buzo puede utilizarse como complemento o

como alternativa al censo tradicional. Su uso puede pro-

porcionar una evaluación más completa, aumentar la adqui-

sición de datos e implementar programas de monitoreo a

largo plazo en áreas donde existen limitaciones económicas

para su operación.

Palabras clave: métodos de muestreo; Maguey; Huatulco;

ictiofauna; Pacífico mexicano.

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