Community structure of Ichneumonidae (Hymenoptera) in a mangrove area in the coastal zone of Tamaulipas, Mexico

Estructura de la comunidad de Ichneumonidae (Hymenoptera) en un área de manglar en la zona costera de Tamaulipas, México

The insect order Hymenoptera includes 3 large groups of parasitic wasps: Chalcidoidea and Braconidae, which are more speciose in the tropics (Horstmann et al., 1999; Noyes, 1989; Wharton et al., 1997) and Ichneumonidae, which are mostly found in temperate zones (Jones et al., 2012; Owen & Owen, 1974; Skillen et al., 2000). Although some authors consider ichneumonids to be an exception to the general trend that on a large-scale species richness increases at lower latitudes (Owen & Owen, 1974; Veijalainen et al., 2012), others have questioned this hypothesis because of description and sampling biases, since small koinobiont species might be overlooked or undersampled in the tropics (Quicke, 2012; Santos & Quicke, 2011; Veijalainen et al., 2013). The abundance and distribution of ichneumonids, similar to all organisms, is determined by climate and availability of resources. However, biodiversity studies are not always related to the sources of variation that influence on distribution patterns of species, such as vegetation types, seasonal climatic changes, and biogeographic distribution (Brown & Maurer, 1989; Clark et al., 2011; Menezes et al., 2015; Poulin et al., 2011; Sääksjärvi et al., 2006; Wolda, 1988).

With a global estimate of 100,000 species (Gauld, 2000), of which more than 24,281 have been described (Yu et al., 2015), the Ichneumonidae is one of the most species-rich animal families in the world (Goulet & Huber, 1993; Triplehorn & Johnson, 2005; Veijalainen et al., 2012). Nearly 7,400 ichneumonid species have been defined as Neotropical, and approximately 7,700 species have been described as Nearctic. In Mexico, where the Nearctic and Neotropical regions converge, approximately 1,300 ichneumonid species have been recorded (Ruíz-Cancino, 2015), of which 59%, 29%, and 10% have Neotropical, both Neotropical and Nearctic and Nearctic distributions, respectively, whereas the remaining species show other trends (Ruíz-Cancino et al., 2014). Extensive faunistic studies of Ichneumonidae have been carried out in Tamaulipas, Veracruz, and Yucatan, which are coastal states on the Gulf of Mexico (Ruíz-Cancino, 2015). However, the fauna of Ichneumonidae have been poorly studied in coastal habitats such as mangroves, which are interesting ecosystems for studying parasitic wasps (Myartseva et al., 2014).

In this study, the community structure of Ichneumonidae in a mangrove area in the southern region of Tamaulipas, Mexico, is described and represents the first study of this family in such habitat. Also, 2 nearby localities with different vegetation types were examined. The study area is characterized as Neotropical, but it is actually on the boundary of the Nearctic region in the northeastern region of the country. Therefore, in this study we evaluated the diversity and species composition of ichneumonid species depending on their biogeographical distribution, type of vegetation, and month of collection.

Materials and methods

Three localities were sampled, which belong to the municipality of Altamira in the state of Tamaulipas, Mexico, at an elevation of 2-15 m asl. These localities correspond to a mangrove area in the Municipality Armenta (22°25’48.30” N, 97°52’34.86” W), a residual low deciduous forest (LDF) in the Congregación Las Prietas (22°31’46.53” N, 97°56’52.86” W), and a low thorny forest (LTF) in the Municipality Aquiles Serdan (22°33’2.87” N, 97°54’13.11” W). The LDF is lush green with dense foliage and a thick herbaceous layer during the rainy season and after the arrival of summer season most trees shed their leaves. The dominant plant genera are Bursera, Phoebe, Chloroleucon, and Acacia (Rzedowski, 2006). The LTF is present in drier sites than those where LDF occurs, with predominance of either evergreen or deciduous thorny trees. The dominant plant genera are Prosopis, Esenbeckia, Pithecellobium, and Acacia (Rzedowski, 2006). The distance among sites is 12-14 km. The weather in the region is predominantly warm and humid with rain in summer. The monthly mean temperature varies from 16.4 °C in January to 25.2 °C in May. The monthly average rainfall varies from 1.8 mm in February to 206.5 mm in September (Table 1) (Conagua, 2012, 2013).

Wasps were captured from May 2012 to April 2013 with Malaise traps that were fabricated based on the design published by Townes (1972). The height of the alcohol pot was approximately 2 m. The Malaise trap color was black, and measured 1.8 m wide by 1.1 m high with a depth of 60 cm for each side. The plastic pot was half full of 95% ethyl alcohol and the samples were collected every 15 days and conserved in refrigeration until examination. One trap was placed in each site. All traps were placed in open areas, oriented with the collector pot toward the east.

Taxonomic determination was carried out using the relevant keys (Brambila, 1997; Dasch, 1979, 1984, 1988, 1992; Gauld, 1988, 1991, 1997, 2000; Gauld et al., 2002; Heinrich, 1977; Kasparyan & Ruíz-Cancino, 2005, 2007, 2008a, 2008b; Khalaim & Ruíz-Cancino, 2012; Reshchikov; 2011; Townes, 1969, 1970a, 1970b, 1971; Townes & Townes, 1978). The specimens that did not match with the morphological features of a described species were regarded as morphospecies. All insects were deposited in the collection of Instituto Tecnológico de Ciudad Victoria, Tamaulipas, Mexico.

Table 1

Monthly temperature and rainfall.

Months	Average monthly temperature (°C)	Monthly rainfall (mm)
May	25.2	14.8
June	24	30.7
July	24.9	115.6
August	24.5	81
September	24.1	206.5
October	21.1	23.6
November	18.7	45.3
December	18.6	2
January	16.4	11.5
February	19.1	1.8
March	17.1	30.3
April	21.2	3

Data analysis

Species accumulation curves were generated for each site using the Clench model, which is an adaptation of the Michaelis-Menten equation that is used to describe the kinetics of enzymatic reactions (Jiménez-Valverde & Hortal, 2003). Because the sites are small, all species have the same probability of being caught, and thus we used the negative exponential equation Clench model (Soberón & Llorente, 1993). The accumulation of species as a function of effort was obtained by the Mao Tau estimator, and the adjustment of the Clench equation was performed with the Quasi-Newton simplex algorithm (StatSoft Statistica 8.0). Alpha diversity was determined at each site from the richness and abundance values using the Simpson index of species evenness and the Shannon-Wiener index of diversity (Magurran, 2004). A t-test was carried out to determine statistically significant differences in Simpson Index data. The Berger-Parker dominance index was used to estimate the proportions of the most abundant species (Moreno, 2001). Differences among sites in the collected species and their abundances were determined by a Permanova multifactorial analysis, which is employed to test the simultaneous response of 1 or more variables to 1 or more factors using permutation methods. This statistic test directly uses the distance matrix to partition the diversity among sources of variation, and is especially suitable for analysis of composition data from ecological studies (Tang et al., 2016). The distance index used was Sorensen-Dice because it assumes imperfect sampling. This analysis was performed with PAST software (version 3.0; Anderson, 2005).

The association of species on type of vegetation, month of collection, and their assigned biogeographical distribution was performed with a multiple correspondence analysis (Abdi & Valentine, 2007; Legendre & Legendre, 2003). The biogeographical distribution of each species was obtained from Yu et al.  (2015), and those cataloged as Neotropical-endemic to Mexico (Nt-End) were based on Ruíz-Cancino (2010). The multiple correspondence analysis is a modification of X² used to analyze multiple categorical variables and creates a Cartesian diagram based on the association among more than 2 categorical variables (Legendre & Legendre, 2003). The diagram displays simultaneously the relative position of the categories of variables studied (Gotelli, 2001). The positions of the categories reflect the degree of association among them, nearest categories of different variable represent a high association, while distant categories show lower association. This analysis was performed with the program Statistica version 12 (StatSoft, 2007).

Results

A total of 770 specimens of Ichneumonidae belonging to 19 subfamilies, 66 genera, and 129 species were collected at the 3 localities (Appendix). The overall capture rate for the study was 0.70 individuals per day-trap and the capture rate of species relative to specimens was 16.8 per 100. The highest relative abundance, with 49.6% of all wasps, was observed in the mangrove habitat; the relative abundances in the LTF and the LDF were 25.7% and 24.7%, respectively. The fewest number of specimens for the 3 sites was obtained in January (25 wasps), whereas March was the most abundant month (107 specimens). The months with more specimens were August, July, and March for the mangrove habitat, LDF, and LTF, respectively. Cryptinae was the most abundant subfamily, represented by 39.6% of the collected specimens (Table 2).  Cryptinae was common in the 3 sites, whereas Rhyssinae was only collected in LDF. Specimens of Brachycyrtinae, Mesochorinae, and Metopiinae subfamilies were only collected in LTF. The most abundant species were Anomalon ejuncidum Say (72 specimens), Eudeleboea subflava Davis (42 specimens), and Pachysomoides stupidus Cresson (42 specimens) (Appendix).

The mangrove area had the highest richness with 88 species of which 31 were exclusive for this site. Sixty-four species (17 exclusive) were collected in LDF, whereas 61 species were collected in LTF (18 were exclusive) (Appendix). The most species-rich subfamilies were Cryptinae (45 species), Cremastinae and Ichneumoninae (both with 16 species), and Campopleginae (14 species). The most species-rich genera were Eiphosoma with 8 species, and Lymeon and Carinodes, with 7 species each.

The maximum values of the Clench function curve for each site are presented in Table 3. The coefficient of determination was greater than 0.9 in all 3 cases, indicating the data were properly matched to the function. This analysis showed that the mangrove site, with 102 estimated species, could potentially be the richest in ichneumonid species of the 3 collected sites. The number of estimated species for the 2 other vegetation types was of 76 in both cases (Table 3).

Comparison of the Ichneumonidae communities at the 3 locations by Permanova showed statistically significant differences (F = 1.95, p = 0.0004) among the sites (Table 4). Thus, the 129 species collected in the study area have clearly different spatial distributions.

These community differences at the 3 sites were not detected in terms of the proportional abundance of each species. That is, the Shannon-Wiener and Simpson indexes were similar for the 3 data sets (Table 5). The t-test carried out on the Simpson index data did not indicate a significant difference between the mangrove and LDF (t₍₄₃₄₎ = -0.924; p > 0.05) or between  LDF and LTF sites (t₍₃₈₇₎ = 1.245; p > 0.05); the only statistically significant difference was detected by comparing the alpha diversity of the mangrove and LTF (t₍₄₄₅₎ = 2.277; p < 0.05). This indicates that the probability of taking 2 individuals of the same species was greater in LTF than in mangrove, and the uncertainty of knowing the identity of a species was greater in mangrove than in LTF. The Berger-Park index, which expresses the number of individuals in proportion to the most abundant species, did not differ between locations (Table 5).

The multiple correspondence analysis (Fig. 1) revealed that biogeographical regions, month of collection, and localities were statistically significant factors (Χ² _d.f.=24,964 = 149,015; p = 0.000) in the community structure of the Ichneumonidae species. The position of categories of biogeographical regions and identity of species was far from the center of graph, and therefore contributes with most of the observed variation. In contrast, the types of vegetation were closer to the center of graph, which means a lower variation. The month of collection had more influence than sites; for example, species cataloged to Nt-End and Nt-Ne regions were most frequent from February to June, and those species from Ne-Nt-Oc-Pa, Ne-Pa-Nt or Nt-Ne-Oc regions were mostly present on August or October. However, some species did not have correspondence with any month or type of vegetation but only with their recorded biogeographical distribution.

Three species collected in this study represent new records for Mexico: Pristomerus jugulator Gauld, 2000, Physotarsus emarginatus Zhaurova, 2009, and Apechoneura mariae Gauld, 2000. Five species, Brachycyrtus cosmetus (Walker, 1956); Pristomerus sulcatus (Cameron, 1908); Temelucha hilux Gauld, 2000; Chirotica confederatae (Ashmead, 1896); and Enicospilus kleini Gauld, 1988, are new records for Tamaulipas.

Table 2

Abundance and species richness per subfamily in the 3 localities.

	Low deciduous forest	Mangrove	Low thorny forest	Total
	Abundance	Richness	Abundance	Richness	Abundance	Richness	Abundance	Richness
Anomaloninae	18	2	49	4	30	4	97	5
Banchinae	8	2	19	2	19	1	46	2
Brachycyrtinae	0	0	2	2	0	0	2	2
Campopleginae	7	3	37	12	7	5	51	14
Cremastinae	8	6	20	8	15	6	43	16
Cryptinae	56	24	176	33	73	23	305	45
Ctenopelmatinae	2	1	2	1	1	1	5	1
Ichneumoninae	27	9	21	8	22	9	70	16
Labeninae	24	4	12	4	5	2	41	5
Lycorininae	1	1	2	1	0	0	3	1
Mesochorinae	0	0	0	0	1	1	1	1
Metopiinae	0	0	0	0	1	1	1	1
Nesomesochorinae	7	1	10	1	8	1	25	1
Ophioninae	9	2	12	2	5	3	26	5
Orthocentrinae	4	2	3	2	9	2	16	2
Pimplinae	11	5	15	6	1	1	27	9
Rhyssinae	3	1	0	0	0	0	3	1
Tersilochinae	0	0	1	1	0	0	1	1
Tryphoninae	5	1	1	1	1	1	7	1

 

Table 3

Data from Clench model at the 3 sites.

	Low deciduous forest	Mangrove	Low thorny forest
Collected species	64	88	61
Percentage of the collected biota	84.03	62.75	80.46
Estimated species	76.15	101.98	75.81
Coefficient of determination (R)	0.9996	0.99894	0.99895

Discussion

This study showed that the community composition of the Ichneumonidae in a mangrove area may significantly differ from nearby areas with different types of vegetation, such as LDF and LTF. In addition, the community structure in this group tend to be determined mostly by the biogeographical distribution of species, followed by the temporal variation throughout the year and less by the type of vegetation. Using multivariate analysis techniques, this study provides a relevant contribution for the Ichneumoid diversity in mangrove areas (Burrows, 2003).

The community of ichneumonids in the mangrove was different in comparison with the other 2 sites. First, the species assemblages of the 3 types of vegetation were significantly different. Second, the abundance and richness were highest in the mangrove area. Third, the local diversity in mangrove was significant higher than LTF, although not different with LDF.

Malaise traps represent a frequently used collecting technique for sampling Ichneumonidae (Fraser et al., 2008; Hall et al., 2015; Pérez-Urbina et al., 2010; Sääksjärvi et al., 2006; Townes, 1972). The overall capture rate for the study was 0.70 individuals per day-trap. This value is in agreement with those reported in other studies, which vary from 2.1 wasps per day-trap (Pérez-Urbina et al., 2010) to low-rate collections of 0.22 individuals per day (Sääksjärvi et al., 2006). However, the capture rate of species relative to specimens was 16.8 per 100. The values found in other studies range from 7 to 17 species per 100 ichneumonids caught (Hall et al., 2015; Pérez-Urbina et al., 2010; Sääksjärvi et al., 2006; Townes, 1971). In comparison, a study with pan traps captured 0.22 species per 100 specimens from a total of 7,500 ichneumonid wasps collected (Gould et al., 2013). Thus, the values of abundance and richness in the present study using Malaise traps are among those obtained by other studies and allowed the determinations of significant statistical differences.

Table 4

P values from Permanova analysis.

Sites	Low deciduous forest	Mangrove	Low thorny forest
Low deciduous forest	–	0.0168	0.0054
Mangrove	0.0168	–	0.0408
Low thorny forest	0.0054	0.0408	–

 

Table 5

Abundance, shared species, exclusive species, and diversity indexes at each site.

Sites	Abundance	Richness of species	Shared species	Exclusive species	Shannon-Wiener	Simpson	Berger-Parker
Low deciduous forest	190	64	47 (73.4%)	17 (26.6%)	3.752	0.0355	0.11053
Mangrove	382	88	57 (64.8%)	31 (35.2%)	3.841	0.0372	0.1021
Low thorny forest	198	61	43 (70.5%)	18 (29.5%)	3.621	0.0401	0.096

Mangroves occur in tropical and subtropical latitudes along coastal intertidal areas (Burrows, 2003). In Mexico, they are distributed inside coastal lagoons and deltaic systems (López & Ezcurra, 2002). Mangroves are forests of salt-tolerant woody plants, often comprising 1 species or a mixture of 3 species of these trees (Burrows, 2003). Although their main feature is general floristic simplicity, mangroves are ecosystems of crucial importance for the life cycles of aquatic fauna (Kathiresan & Bingham, 2001). The legal protection in Mexico is based on their ecological relevance (Moral-Padilla et al., 2012). Entomofaunistic studies of these ecosystems usually assess plant-insect relationships through herbivory (Burrows, 2003; Feller & Chamberlain, 2007; Feller & Mathis, 1997; Murphy & Lugo, 1986). However, there are few studies in other trophic guilds. The only faunistic study of parasitioid and predatory insects in mangroves was carried out by Veenakumari et al. (1997) on 2 Indian islands. These authors suggested that these kinds of forests cannot sustain a large population of insects, but they are influenced by their adjacent areas (Berjak et al., 1977; Kathiresan & Bingham, 2001; Veenakumari et al., 1997). Thus, the richness of Ichneumonidae collected in the mangrove area in this study could result from the mutual influences of the mangrove and its surroundings. Rao et al. (1998) had already mentioned that mangrove insect visitors could function as links between these aquatic ecosystems and neighboring areas.

In this study, the community structure of Ichneumonidae was strongly determined by the biogeographical distribution where species were reported. The relative abundances of species showed strongest correspondence with the biogeographical categories compared to collecting month and type of vegetation. Neotropical (Nt, Nt-Ne, Nt-End) species, which were the most abundant, were collected throughout all months of the year, although their frequency was lower in August, October, and November. The frequency of Nt-End and Nt-Ne species was associated with the months from February to June, when the temperature ranged from 19.1-24 ^°C and the rainfall from 1.8 mm to 30.7 mm. In comparison, the most-rainy months were July (311 mm) and September (314 mm), but their association with the relative abundance of the species was lower, since the associated species tend to be cosmopolites. With respect to types of vegetation, the correspondence was lower than the collecting month. These data indicate that the zone is markedly Neotropical with a good established community of ichneumonids, despite fluctuations of temperature and precipitation through the year.

In conclusion, the community structure of the ichneumonid wasps in the subtropical zones near to Nearctic region strongly depends on the biogeographical distribution of the species in association with climatic variation throughout the year. However, the mangrove and their surroundings appear to be favorable for this group of insects, which is a relevant issue given the limited information of parasitic Hymenoptera in this ecosystem.

Finally, with the new records for Mexico and Tamaulipas presented here, knowledge about the geographical distribution of some species has been extended. Based on this, 1,306 species of Ichneumonidae fauna are now registered for Mexico (Ruíz-Cancino, 2015) and 417 species are reported for the state of Tamaulipas (Ruíz-Cancino, 2010).

Acknowledgments

We thank the Consejo Nacional de Ciencia y Tecnología for the support through the scholarship for postgraduate studies granted to the first author and Grant No. 219583 (CB-2013-01) to CSVB.

Appendix. List of species of Ichneumonidae collected in this study. Nt: Neotropical, Ne: Nearctic, Pa: Palearctic, Or: Oriental, Oc: Oceanic, Co: Cosmopolitan, Et: Ethiopic, Au: Australian, End: Endemic to Mexico. LDF: low-stature deciduous forest, MGR: mangrove, LTF: low-stature thorny forest. *New records to Tamaulipas, **New records to Mexico.

	Subfamily Species/Morphospecies	Biogeography	LDF	MGR	LTF	♀/♂	Total
I.	Anomaloninae
1	Anomalon constrictum Dasch, 1984	Nt, Ne	0	0	5	5/0	5
2	Anomalon ejuncidum Say, 1835	Ne, Nt	16	38	18	72/0	72
3	Anomalon fuscipes (Cameron, 1886)	Nt	0	1	1	2/0	2
4	Corsoncus minori Gauld y Bradshaw, 1997	Nt	0	1	0	1/0	1
5	Ophiopterus cincticornis (Cresson, 1865)	Ne, Nt	2	9	6	16/1	17
II.	Banchinae
6	Diradops hyphantrinae Kasparyan y Pinson, 2007	Nt (End)	2	2	0	4/0	4
7	Meniscomorpha subflava (Davis, 1898)	Ne, Nt	6	17	19	30/12	42
III.	Brachycyrtinae
8	Brachycyrtus cosmetus (Walkley, 1956)*	Nt	0	1	0	1/0	1
9	Brachycyrtus pretiosus Cushman, 1936	Nt	0	1	0	1/0	1
IV.	Campopleginae
10	Campoletis sp. Förster, 1869	Co	0	5	0	5/0	5
11	Casinaria sp. 1 Holmgren, 1859	Co	0	2	1	2/1	3
12	Casinaria sp. 2  Holmgren, 1859	Co	0	2	1	1/2	3
13	Casinaria sp. 3  Holmgren, 1859	Co	0	0	2	2/0	2
14	Diadegma sp. 1 Förster, 1869	Co	0	2	0	2/0	2
15	Diadegma sp. 2 Förster, 1869	Co	0	2	0	1/1	2
16	Dusona sp. Cameron, 1901	Co	0	1	0	1/0	1
17	Echthronomas sp. Förster, 1869	Ne, Pa, Or	1	5	0	6/0	6
18	Microcharops sp. Roman, 1910	Nt, Ne, Pa	4	11	0	13/2	15
19	Phobocampe sp.  Förster, 1869	Ne, Pa, Nt	2	0	2	4/0	4
20	Venturia sp. 1 Schrottky, 1902	Co	0	4	1	5/0	5
21	Venturia sp. 2 Schrottky, 1902	Co	0	1	0	1/0	1
22	Venturia sp. 3 Schrottky, 1902	Co	0	1	0	1/0	1
23	Xanthocampoplex sp. Morley, 1913	Et, Au, Pa, Ne	0	1	0	1/0	1
V.	Cremastinae
24	Eiphosoma sp. 1 Cresson, 1865	Nt, Ne, Oc	0	0	1	1/0	1
25	Eiphosoma sp. 2 Cresson, 1865	Nt, Ne, Oc	0	0	1	1/0	1
26	Eiphosoma batatae Cushman, 1931	Nt	0	2	0	2/0	2
27	Eiphosoma dentator (Fabricius, 1804)	Nt, Ne, Oc	0	1	1	2/0	2
28	Eiphosoma macrum (Enderlein, 1921)	Nt	0	0	3	2/1	3
29	Eiphosoma mexicanum Cresson, 1874	Nt, Ne	0	1	0	0/1	1
30	Eiphosoma nigrolineatum (Brullé, 1846)	Nt, Ne	1	0	0	0/1	1
31	Eiphosoma vitticolle Cresson, 1865	Nt, Ne	0	2	0	1/1	2
32	Pristomerus jugulator Gauld, 2000**	Nt	1	0	0	0/1	1
33	Pristomerus spinator (Fabricius, 1804)	Ne, Nt, Oc	0	1	0	1/0	1
34	Pristomerus sulcatus (Cameron, 1908)*	Nt	0	8	3	10/1	11
35	Temelucha hilux Gauld, 2000*	Nt	1	1	0	2/0	2
36	Temelucha sp. Förster, 1869	Co	1	0	0	1/0	1
37	Xiphosomella dubia (Brues, 1911)	Ne	1	4	0	2/3	5
38	Xiphosomella sp. 1 Szépligeti, 1905	Nt, Ne	0	0	6	5/1	6
39	Xiphosomella sp. 2 Szépligeti, 1905	Nt, Ne	3	0	0	2/1	3
VI.	Cryptinae
40	Acerastes accolens (Cresson, 1874)	Nt (End)	1	5	0	2/4	6
41	Acerastes faciator Kasparyan et Ruíz, 2008	Nt (End)	2	0	2	4/0	4
42	Acerastes myartsevae Kasparyan et Ruíz, 2008	Nt (End)	0	0	1	1/0	1
43	Acerastes pertinax (Cresson, 1872)	Nt (End)	2	2	6	3/7	10
44	Acerastes scabrosus Kasparyan et Ruíz, 2008	Nt (End)	2	0	4	3/3	6
45	Acerastes tinctor Kasparyan et Ruíz, 2008	Nt (End)	0	0	7	7/0	7
46	Agonocryptus chichimecus (Cresson, 1874)	Nea, Neo	5	17	16	18/20	38
47	Baryceros zapotecus (Cresson, 1874)	Nt (End)	0	2	0	2/0	2
48	Basileucus suspiciosus Kasparyan et Ruíz, 2008	Nt (End)	0	1	0	1/0	1
49	Cestrus arcuatorius Kasparyan et Ruíz, 2005	Nt (End)	10	3	0	4/9	13
50	Chirotica confederatae (Ashmead,1896)*	Ne	0	1	1	2/0	2
51	Cryptanura brachygaster (Cameron, 1885)	Nt (End)	0	5	1	3/3	6
52	Cryptanura lunai Kasparyan y Ruíz, 2006	Nt (End)	0	0	1	0/1	1
53	Diapetimorpha acadia Cushman, 1929	Ne, Nt	1	0	0	1/0	1
54	Diapetimorpha communis (Cresson, 1874)	Ne, Nt	2	1	0	1/2	3
55	Diapetimorpha macula (Cameron, 1886)	Ne, Nt	5	1	4	10/0	10
56	Diapetimorpha monilis (Cresson, 1874)	Nt	0	1	0	1/0	1
57	Diapetimorpha pedator Kasparyan et Ruíz, 2005	Nt (End)	1	0	1	0/2	2
58	Diapetimorpha scitula (Cresson, 1874)	Nt (End)	3	4	5	8/4	12
59	Digonocryptus thoracicus Kasparyan et Ruíz, 2005	Nt	4	11	0	10/5	15
60	Digonocryptus variegatus (Szépligeti, 1916)	Nt	0	1	0	1/0	1
61	Epicnemion lineator Kasparyan et Ruíz, 2008	Nt (End)	0	1	0	1/0	1
62	Gambrus bituminosus (Cushman, 1924)**	Ne	0	1	0	1/0	1
63	Gambrus ultimus (Cresson, 1864)	Ne, Nt, Oc	1	0	0	1/0	1
64	Joppidium brochum Townes, 1962	Ne, Nt	4	0	0	1/3	4
65	Latosculum ruizi Kasparyan, 2004	Nt (End)	0	3	0	1/2	3
66	Lymeon acceptus (Cresson, 1874)	Nt (End)	0	1	1	1/1	2
67	Lymeon mandibularis Kasparyan y Ruíz, 2004	Nt (End)	1	0	0	0/1	1
68	Lymeon minutus Kasparyan y Ruíz, 2008	Nt (End)	1	10	4	14/1	15
69	Lymeon moratus (Cresson, 1874)	Nt (End)	3	22	5	15/15	30
70	Lymeon rufotibialis Kasparyan y Ruíz, 2004	Nt (End)	0	1	3	4/0	4
71	Lymeon tantillus (Cressson, 1874)	Nt (End)	2	5	1	5/3	8
72	Lymeon tricoloripes Kasparyan y Ruíz, 2004	Nt (End)	1	1	1	2/1	3
73	Mallochia sp. Viereck, 1912	Ne, Nt	1	0	0	0/1	1
74	Messatoporus compressicornis Cushman, 1929	Ne, Nt	1	12	1	9/5	14
75	Messatoporus discoidalis (Cresson, 1872)	Ne, Nt	1	0	0	0/1	1
76	Messatoporus mesonotator Kasparyan y Ruíz, 2005	Nt (End)	0	2	0	2/0	2
77	Messatoporus propodeator Kasparyan y Ruíz, 2005	Nt (End)	0	1	0	0/1	1
78	Pachysomoides stupidus (Cresson, 1874)	Nt, Ne	0	39	3	42/0	42
79	Polycyrtidea carlosi Kasparyan et Ruíz, 2008	Nt (End)	1	2	0	1/2	3
80	Polycyrtidea limitis Cushman, 1929	Nt, Ne	0	2	0	2/0	2
81	Polycyrtus melanoleucus (Brullé, 1846)	Nt	1	4	1	3/3	6
82	Polycyrtus semialbus (Cresson, 1865)	Nt	0	11	0	8/3	11
83	Polycyrtus sp. Spinola, 1840	Nt, Ne	0	1	3	4/0	4
84	Xenarthron pectoralis Kasparyan et Ruíz, 2005	Nt (End)	0	2	1	3/0	3
VII.	Ctenopelmatinae
85	Physotarsus emarginatus Zhaurova, 2009**	Ne	2	2	1	5/0	5
VIII.	Ichneumoninae
86	Carinodes sp. 1 Hancock, 1926	Nt, Ne	8	2	9	18/1	19
87	Carinodes sp. 2 Hancock, 1926	Nt, Ne	3	5	0	7/1	8
88	Carinodes sp. 3 Hancock, 1926	Nt, Ne	2	0	5	0/7	7
89	Carinodes sp. 4 Hancock, 1926	Nt, Ne	3	0	0	3/0	3
90	Carinodes sp. 5 Hancock, 1926	Nt, Ne	2	0	0	0/2	2
91	Carinodes sp. 6 Hancock, 1926	Nt, Ne	0	0	1	1/0	1
92	Carinodes sp. 7 Hancock, 1926	Nt, Ne	0	0	1	0/1	1
93	Lobaegis arista (Cresson, 1868)	Nt (End)	2	3	0	3/2	5
94	Oedicephalus sp. Cresson, 1868	Nt	1	1	1	2/1	3
95	Phaeogenes sp. Wesmael, 1845	Ne, Pa, Or	0	3	0	3/0	3
96	Projoppa sp. Townes, 1966	Nt	4	4	1	7/2	9
97	Tricholabus sp. 1 Thomson, 1894	Nt, Pa, Ne, Or	0	0	2	2/0	2
98	Tricholabus sp. 2 Thomson, 1894	Ne, Pa, Nt, Or	0	2	0	0/2	2
99	Tricholabus sp. 3 Thomson, 1894	Ne, Pa, Nt, Or	0	1	1	0/2	2
100	Tricholabus sp. 4 Thomson, 1894	Ne, Pa, Nt, Or	0	0	1	1/0	1
101	Trogomorpha arrogans (Cresson, 1874)	Nt, Ne	2	0	0	1/1	2
IX.	Labeninae
102	Apechoneura mariae Gauld, 2000**	Nt	1	1	0	2/0	2
103	Grotea fulva Cameron, 1886	Nt	1	3	0	4/0	4
104	Labena eremica Gauld, 2000	Nt	20	6	3	10/19	29
105	Labena schausi Cushman, 1922	Nt	0	2	0	2/0	2
106	Labena tarsata Gauld, 2000	Nt	2	0	2	2/2	4
X.	Lycorinae
107	Lycorina apicalis Cresson, 1874	Nt, Ne	1	2	0	2/1	3
XI.	Mesochorinae
108	Mesochorus sp. Gravenhorst, 1829	Co	0	0	1	1/0	1
XII.	Metopiinae
109	Metopius errantia Davis, 1897	Ne	0	0	1	0/1	1
XIII.	Nesomesochorinae
110	Nonnus sp. Cresson, 1874	Nt	7	10	8	9/16	25
XIV.	Ophioninae
111	Enicospilus glabratus (Say, 1835)	Nt, Ne	0	4	0	4/0	4
112	Enicospilus kleini Gauld, 1988*	Nt	1	0	0	1/0	1
113	Enicospilus masoni Gauld, 1988*	Nt	0	0	1	1/0	1
114	Enicospilus purgatus (Say, 1835)	Ne, Nt, Oc	0	0	3	3/0	3
115	Enicospilus trilineatus (Brullé, 1846)	Nt, Ne, Oc	8	8	1	14/3	17
XV.	Orthocentrinae
116	Megastylus sp. Schiødte, 1838	Co	1	2	8	10/1	11
117	Orthocentrus sp. Gravenhorst, 1829	Co	3	1	1	5/0	5
XVI.	Pimplinae
118	Clistopyga calixtoi Gauld, 1991	Nt	0	0	1	1/0	1
119	Clydonium quintanillai Gauld, 1991	Nt	0	2	0	2/0	2
120	Neotheronia mellosa (Cresson, 1874)	Nt	4	0	0	2/2	4
121	Neotheronia tacubaya (Cresson, 1874)	Nt	0	2	0	0/2	2
122	Pimpla punicipes Cresson, 1874	Nt, Ne, Oc	3	4	0	0/7	7
123	Pimpla sanguinipes Cresson, 1872	Ne, Nt	2	4	0	5/1	6
124	Pimpla sumichrasti Cresson, 1874	Nt	1	2	0	2/1	3
125	Scambus sp. Hartig, 1838	Ne, Nt, Oc, Pa	1	0	0	0/1	1
126	Zatypota alborhombarta (Davis, 1895)	Nt, Ne	0	1	0	1/0	1
XVII.	Rhyssinae
127	Epirhyssa mexicana Cresson, 1874	Nt, Ne	3	0	0	0/3	3
XVIII.	Tersilochinae
128	Allophrys divaricata Horstmann, 2010	Nt, Ne	0	1	0	1/0	1
XIX.	Tryphoninae
129	Netelia sp. Gray, 1860	Co	5	1	1	7/0	7
		Total	190	382	198	555/215	770

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