Biodiversity, distribution, ecology and management of non-native weeds in Mexico: a review

Non-native, also known as exotic, species are increasingly found in all ecosystems, mainly in those directly disturbed by humans. A small fraction of the bulk of non-native plant species introduced in a country become invaders ( Williamson & Fitter, 1996 ), causing human health, environmental, or economic damage, mainly at the local scale ( Powell, Chase, & Knight, 2011 ). Although the biological invasion process is well described ( Richardson et al., 2000 ), including the major pathways naturalized plants follow in new ranges ( van Kleunen et al., 2015 ), the prediction of which non-native species will behave as invasive in the new range is not accurate enough. The complexity of biological invasions has not allowed a full theoretical understanding of the phenomenon ( Kueffer, Pysek, & Richardson, 2013 ), in spite of an exponential growth of research on biological invasions since 1990 (44,111 scientific papers published in the 2010–2015 period out of 70,400 studies published between 1900 and 2015) (ISI Web of Science search of “biological invasions” in December, 2015). Thus, management decisions ranging from prevention to mitigation have been based on a mixture of empirical and scientifically based information as not enough scientific knowledge is available for the myriad of conditions in which biological invasions occur.

The environmental and economic damage caused by invasive species is of such magnitude, at least 1.4 trillion US dollars globally ( Diversitas, 2010 ), that it has prompted international attention through global initiatives that foster scientific research and societal attention to manage and prevent biological invasions. For example, the Global Invasive Species Programme (GISP) (1997–2010) sponsored by DIVERSITAS, was founded to provide support to the Convention of Biological Diversity (CDB). GISP proposed, among other things, a framework to investigate the ecology and the socioeconomic factors involved in biological invasions and their management ( Mooney, 2005 ). For Mexico, the CBD and GISP were instrumental for the National Commission on Biodiversity (Comisión Nacional para el Conocimiento y Uso de la Biodiversidad, Conabio) in fostering the National Strategy on Invasive Species in Mexico, prevention, control and eradication ( Comité Asesor Nacional sobre Especies Invasoras, 2010 ). Under these worldwide conditions of scientific and empirical knowledge on invasive species, we briefly review the research regarding non-native weeds in Mexico published up to 2015. We then evaluate the advances represented in the Mexican scientific literature on non-native weeds considering the strategic objectives on prevention, early detection and rapid response, containment and mitigation proposed by the National Strategy on invasive species in Mexico: strategic objective 1, “Prevent, detect and reduce the risk of introduction, establishment and dispersal of invasive species”; strategic objective 2, “Establish control and eradication programs for invasive species’ populations, which minimize or eliminate their negative impacts and favor ecosystem restoration and conservation”; strategic objective 3, “Inform the public in an appropriate and efficient way to achieve a broad civil support and participation within their reach in actions to prevent, control and eradicate invasive species”.

Methods

We used references within previous accounts on research and management of non-native plant species in Mexico ( Espinosa-García, 2009; Espinosa-García, Villaseñor, & Vibrans, 2009 ), as well as the authors’ personal libraries, and a key word search in the ISI Web of Science database encompassing published literature from 1950 to 2015. The keywords used for the search were “invasive plant* AND Mexico”; “invasive weed* AND Mexico”; “exotic plant* AND Mexico”; “exotic weed* AND Mexico”; “introduced plant* AND Mexico”; “introduced weed* AND Mexico”; “alien plant* AND Mexico”; “alien weed* AND Mexico”. In most cases these searches were limited to authors or coauthors with Mexican addresses, but we excluded studies performed in other countries with participation of authors from Mexican institutions. From personal libraries we included publications on non-native species in Mexico from researchers without Mexican addresses (e.g. Williams, 2010 ). We estimate that we included most refereed publications not indexed in the Web of Science, although it is very likely that some were missed. We are not including most B.Sc. and M.Sc. thesis, non-refereed-congress proceedings or abstracts (e.g. Memories of the Mexican Weed Society (ASOMECIMA) meetings), and technical reports from field research stations which are usually not refereed nor included in ISI Web of Science. Most of these publications report important research on weeds (mainly management) but the distinction between native and exotic weed species is usually lacking and they have very limited accessibility.

Results

We found 229 papers, chapters or books on: non-native algae (7), ferns (6) and flowering plants (216) published between 1939 and 2015. Here we review the publications of non-native wild flowering plants.

Publication topics

The publications’ topics are represented in Figure 1 . Most papers (34.5%) deal with management sensu lato , including restoration, and chemical, cultural or biological control; 21.5% with several ecological topics; 19.5% of papers deal with floristics; 13% with detection of new non-native weeds, usually accompanied by the distribution range when the non-native was discovered; 8% deal with actual and potential distribution of naturalized or invasive plants; 6% deal with the economic or ecological impact of non-native weeds; and finally 3% deal with non-native species uses or ethnobotany. Percentages add up to 105.5% as there were publications included in more than 2 topics. Publications that covered more than one topic were assigned to their predominant one; if 2 or more predominated equally, then the publications were considered in more than one topic.

Publications on non-native species throughout time

Schinus molle L., the pirú or pirul tree, was introduced in the New Spain, now Mexico, by the viceroy Antonio de Mendoza in the XVI century; the introduction, dispersal and uses were documented by Alzate and Ramírez 1791, Gómez 1889–1890, Jiménez 1873, Herrera 1896 and López y Parra 1899 (authors cited in Corkidi, Cacho, & Búrquez, 1991 ). Although no other purposeful introduction of a species was documented, botanists in Mexico have been well aware of introduced wild species since the early 20th century. For example, in “La Flora Excursoria en el Valle Central de México” ( Reiche, 1926 ) several naturalized species are reported as coming from the “old world” such as Avena fatua L. and Helminthotheca echioides (L.) Gaertn (=Picris echioides L.). However, this kind of publications did not go beyond mentioning the continent of origin of the naturalized species. Thus, we concentrated on publications dedicated predominantly on non-native naturalized and/or invasive species or to those that compare native with non-native flora. Adding up the results of the ISI Web of Science and the bibliographic resources of the authors, we found 229 published articles or book chapters dealing with non-native algae (7), ferns (6) and flowering plants (216) in a period going from 1939 through 2015. The first two papers on invasive plants were published by the prominent agronomist Gabriel Itie ( Cotter & Osborne, 1996 ). The first paper was published on Urochloa mutica (Forssk.) T.Q. Nguyen (= Panicum purpurescens Raddi), a grass introduced as forage and later escaped and became naturalized ( Itié, 1939). In 1945 a paper appeared on Melinis repens (Willd.) Zizka, an African grass introduced in the 1930s to be tested as forage ( Itié, 1945 ). This grass failed as a forage crop but escaped, mainly along roads and highways. It is now an invasive plant that has colonized roadsides all over Mexico encroaching on semi-desert scrublands, orchards and vegetation adjacent to roads and highways ( Díaz-Romo et al., 2012; Melgoza-Castillo, Balandrán-Valladares, Mata-González, & Pinedo-Álvarez, 2014 ). There were no publications on non-native plants up to 1959, when Dr. Jerzy Rzedowsky directed his scholarly attention to invasive species documenting the spread of the invasive Salsola kali L. var. tenuifolia Tausch (Rzedowski, 1959 ). His attention continued to date, recognizing invasive species together with his wife in the Floras published by Rzedowski and Calderon-de Rzedowski (Flora Fanerogámica del Valle de México and Flora del Bajío), and detecting new non-native species ( Calderón-de Rzedowski & Rzedowski, 2004; Calderón-de Rzedowski et al., 2001; Rzedowski & Calderón-de Rzedowski, 1985, 2005; Rzedowski, Vibrans, & Calderón-de Rzedowski, 2003 ). In 1971, a pioneer work on allelopathy of a non-native species, S. molle was published (Anaya & Gómez-Pompa, 1971 ). We detected no new publications until the 1980s, where 7 papers where published, one on urban floristics distinguishing native and non-native weeds ( Rapoport, Díaz-Betancourt, & López-Moreno, 1983 ), 2 on non-native species detection ( Espinosa-García, 1981; Lot, Novelo, & Cowan, 1980 ), 2 on chemical control ( Magallanes, Ortiz, & Rojas-Garcidueñas, 1986; Tamayo-Esquer & Gaillardon, 1989 ) and 2 on ecological aspects of Nicotiana glauca Graham (Hernández, 1981) and Eichhornia crassipes (C. Mart.) Solms. ( Niño-Sulkowska & Lot, 1983). In the1990s, after Rzedowski and Calderón-de Rzedowski (1990) published an important paper on African weeds naturalized in Mexico, a paper on the dispersal of S. molle by birds (Corkidi et al., 1991 ) together with another important paper on the sinanthropic Asteraceae in Mexico ( Rzedowski, 1993 ), a fluctuating increase in publication is observed through 2015 ( Fig. 2 ). Although the publication increase is notorious since 1999, it is far from the huge increase in international publications. The fluctuations are probably related to the activity of a few individuals who have a primary, but not unique, interest on non-native plants. For example, the authors publishing new reports of non-native species ( Table 2 ) are or were primarily agronomists, taxonomists, specialists in floristics, ethnobotanists or ecologists.

Figure 1

Percentage of publciations on non-native weedy flowering plants in Mexico in 1939–2015 on major research topics. Percentages add up to 105.5% as there were publications included in more than 2 topics. Sources: ISI Web of Knowledge; Espinosa-García (2009); Espinosa-García et al. (2009) ; FJE and JLV personal libraries.

Figure 2

Refereed publications on non-native flowering plants published by authors with Mexican address (n = 216). Data obtained from 216 publications obtained from the sources mentioned in Figure 1.

Floristics and detection of new non-native species for Mexico

Dealing with invasive weeds requires extensive knowledge of the identity and distribution of the non-native plant species that have entered a country, established, naturalized, and became invasive (i.e. cause damage) or pests (i.e. noxious or destructive). Although the number of publications on floristics or detection of new non-native weeds is not the majority (20% of total publications), the families with introduced species in Mexico is well known ( Espejo-Serna, López-Ferrari, & Ugarte, 2004 ), as well as the list of most non-native species following the papers by Villaseñor and Espinosa-García (1998, 2004) and Espinosa-García et al. (2009) .

In 2004, 618 non-native species were reported for Mexico ( Villaseñor & Espinosa-García, 2004 ); with 22 species added in 2009 ( Espinosa-García et al., 2009 ). In this review, 31 previously undetected species have been added ( Table 1 ), but recent reviews of the non-native weedy Poaceae and Asteraceae ( Sánchez-Ken, Zita-Padilla, & Mendoza-Cruz, 2012; Villaseñor, Ortiz, Hinojosa-Espinosa, & Segura-Hernández, 2012 ), changed the non-native status of 39 species, but reported 40 previously undetected wild species, many of them formerly known as ornamentals. Additionally, JLV has detected 26 more species in his database (not reported here). These data add up to 698 non-native species registered for Mexico, but recent publications (not included in this review) enlist additional non-native species with unknown wild or cultivated status. We are currently revising the entire list of wild non-native species in Mexico for a future publication, but we estimate that the actual figure for wild non-native species for Mexico to be in the order of 700–750 species.

Table 1

Recently detected non-native weed species not enlisted in Villaseñor and Espinosa-García (2004) . Update from the list published in Espinosa-García et al. (2009) .

Family	Species	Origin	Comments
Alismataceae	Sagittaria sagittifolia L.	Europe	EDOMEX h t t p & # 5 8 ; & # 4 7 ; & # 4 7 ; w w w & # 4 6 ; e d o m e x ico.gob.mx/sma/se/BIO_INTERNET/monografias.html seen on 25/04/2007; h t t p & # 5 8 ; & # 4 7 ; & # 4 7 ; w w w & # 4 6 ; i s s g & # 4 6 ; o r g & # 4 7 ; d a t a b a s e & # 4 7 ; s p e c i e s & # 4 7 ; d i s t r i b u t i o n & # 9 5 ; d i s p l a y & # 4 6 ; a s p & # 6 3 ; s i & # 6 1 ; 8 5 8 & # 38;ri=18917&pc=*&sts=sss&status=Alien#Alien seen on 5/03/2007
Apiaceae	Cuminum cyminum L.	Mediterranean	CHIH, VER (Williams, 2010)
Asteraceae	Arctotheca prostrata (Salisb.) Britten	South Africa	DF ( Hinojosa-Espinosa & Villaseñor, 2015 )
Asteraceae	Carduus nutans L.	Eurasia	HGO (Williams, 2010)
Asteraceae	Crepis capillaris (L.) Wallr.	Europe	VER. Naturalizada, ruderal y en agostaderos ( Rzedowski & Calderón-de Rzedowski, 2005 )
Brassicaceae	Chorispora tenella (Pall.) DC.	Eurasia	SON (Van Devender & Reina, 2007)
Brassicaceae	Sisymbrium erysimoides	Mediterranean	EDOMEX, Heike Vibrans (Vibrans 8076, MEXU, CHAPA) (Vibrans, 2010)
Caesalpiniaceae	Senna polyantha (Collad.) H.S. Irwin & Barneby	Africa	BC 11 estados (Villaseñor & Espinosa-García, unpublished data)
Chenopodiaceae	Dysphania botrys (L.) Mosyakin & Clemants = Chenopodium botrys L.	Mediterranean	CHIH (Williams, 2010)
Chenopodiaceae	Salsola paulsenii Litv.	Asia	CHIH (Williams, 2010)
Convolvulaceae	Convolvulus crenatifolius Ruiz & Pavón	South America	DF, EDOMEX, GTO, HGO, JAL, MICH, QRO ( Carranza-González, 2005)
Convolvulaceae	Ipomoea wrightii A. Gray.	Unknown	CAM, JAL, SON, TAB, YUC ( Williams, 2010) ( http://bios.conabio.gob.mx/especies/6076916 )
Euphorbiaceae	Phyllanthus urinaria L.	Sri Lanka and southeast Asia.	CHIS, OAX, VER (Williams, 2010)
Fabaceae	Abrus precatorius L.	India	CAM, VER, YUC. (Villaseñor & Espinosa-García, unpublished data)
Fabaceae	Albizia lebbeck (L.) Benth.	Tropical Asia	CAM, SIN, TAM (Williams, 2010)
Fabaceae	Lotus corniculatus L.	Eurasia	BC (Williams, 2010)
Fumariaceae	Fumaria officinalis L.	Europe	SON (Van Devender & Reina, 2007)
Lamiaceae	Vitex agnus-castus L.	Mediterranean	NL (Williams, 2010)
Liliaceae	Nothoscordum inodorum (Ait.) Nicholson	South America	MICH (Williams, 2010)
Malvaceae	Abutilon theophrasti Medik.	Southern Asia	EDOMEX (Domínguez & Pitalúa, unpublished data; Vibrans, unpublished data), SON ( Van Devender & Reina, 2007)
Mimosaceae	Acacia tortuosa (L.) Willd.	Tropical Asia	COL, DGO, HGO, JAL, MICH, OAX, SLP, TAM, SLP (Villaseñor & Espinosa-García, unpublished data)
Moraceae	Morus alba L.	China	COAH, SON, TAMS (Williams, 2010)
Papaveraceae	Fumaria officinalis L.	Europe	SON (Williams, 2010)
Papaveraceae	Glaucium corniculatum (L.) Rudolph	Eurasia	SON (Van Devender & Reina, 2007)
Poaceae	Cenchrus brownii Roem. & Schult.	South Africa or Tropical America	All México (Villaseñor & Espinosa-García, unpublished data)
Poaceae	Chloris barbata Sw.	Africa	VER (Williams, 2010)
Poaceae	Cortaderia selloana (Schult. & Schult. f.) Asch. & Graebn.	South America	Widely cultivated, feral in EDOMEX (Vibrans 8055, CHAPA)
Poaceae	Eragrostis ciliaris (L.) R. Br.	Cosmopolitan	BC, CAM, CHIS, COL, GRO, JAL, MEX, MICH, MOR, NAY, OAX, PUE, QROO, SLP, SIN, SON, TAB, TAM, VER, YUC ( Martin et al., 1998; h t t p ://mobot.mobot.org/cgi-bin/search_vast#meso seen on November 13, 2007)
Poaceae	Eragrostis echinochloidea Stapf	Africa	SON (Van Devender & Reina, 2007)
Poaceae	Hyparrhenia cymbaria (L.) Stapf,	Africa	Vibrans, García-Moya, Clayton, & Sánchez-Ken (2014)
Poaceae	Hyparrhenia variabilis Stapf	Africa	Vibrans et al. (2014)
Poaceae	Panicum coloratum L.	Africa	NL (Williams, 2010)
Poaceae	Setaria pumila (Poir.) Roem. & Schult.	Eurasia	NL, SON (Williams, 2010)
Poaceae	Themeda quadrivalvis (L.) Kuntze	Africa	MOR ( Sánchez-Ken, Cerros-Tlatilpa, & Vibrans, 2013 )
Polygonaceae	Polygonum nepalense Meisn.	Asia	EDOMEX (Vibrans & Alipi, 2008 , Vibrans 8036, MEXU, CHAPA)
Polygonaceae	Rumex dentatus L.	Eurasia	SON, TAM (Villaseñor & Espinosa-García, unpublished data)
Polygonaceae	Rumex stenophyllus Ledeb.	Europe	SON (Martin et al., 1998)
Ranunculaceae	Ranunculus sardous Crantz	Old World	PUE ( Hanan-Alipi, Mondragón-Pichardo, & Vibrans, 2005 )
Rosaceae	Prunus persica (L.) Batsch	Asia	SON (Van Devender & Reina, 2007)
Rubiaceae	Pentodon pentandrus (Schumach. & Thonn.) Vatke	Brazil	TAM, VER, NL (Villaseñor & Espinosa-García, unpublished data)
Scrophulariaceae	Verbascum blattaria L.	Eurasia	CHIH (Williams, 2010)
Simaroubaceae	Ailanthus altissima (Mill.) Swingle	China	CHIH, COAH (Williams, 2010)
Solanaceae	Solanum sisymbriifolium Lam.	South America	CAM, CHIH, JAL, SON, VER ( Martin et al., 1998; Van Devender & Reina, 2007 )
Verbenaceae	Glandularia tenuisecta (Briq.) Small	South America	SON (Martin et al., 1998)
Verbenaceae	Verbena brasiliensis Vell.	South America	NAY, NL (Williams, 2010)

 

It is likely that several newly detected species have been present in Mexico long before and had not been detected due to under exploration or because they were overlooked or misidentified in herbarium collections ( Villaseñor et al., 2012). For example, Williams (2010) reported 24 non-native species for Mexico not listed by Villaseñor and Espinosa-García (2004) based on herbarium records and field work. Herbarium records were also of crucial importance in the studies of Sánchez-Ken et al. (2012) and Villaseñor et al. (2012) . Other potential sources of newly naturalized non-native species are the cultivated or ornamental species becoming feral. Ornamental, forage or crop escapees constitute a large proportion of naturalized non-native species in various floras ( Dehnen-Schmutz, Touza, Perrings, & Williamson, 2007; Mack, 2000 ), but they are often overlooked when they become feral. Thus, we suspect that between one third and one half of the detected species between 2004 and 2015 arrived recently to Mexican territory.

Assuming that the non-native status change for 39 species ( Sánchez-Ken et al., 2012 ) is confirmed, and the actual species number is ca. 700, then 121 new non-native species for Mexico were added between 2004 and 2015; this means that, on average, around 13 species per year were recorded. This number doubles the estimate by Espinosa-García et al. (2009) and is much higher than the 5 species per year calculated for the 1930–2008 period in the United States Pacific Northwest ( Stohlgren, Barnett, Jarnevich, Flather, & Kartesz, 2008 ).

The detection of most new non-native species has been mainly the result of the activity of few professional botanists with long trajectory in floristics and/or taxonomy, such as J. Rzedowski and G. Calderón-de Rzedowski, Heike Vibrans, José Luis Villaseñor and Tom Van Devender among others ( Table 2 ). This activity is adequate but insufficient, as Mexico is a large country (1,964,375 km2 ) and a formal early detection program is needed.

Table 2

Publications reporting previously undetected non-native species from 1939 to 2015.

1939	Itié (1939), Urochloa mutica (Forssk.) T.Q. Nguyen (Poaceae)
1945	Itié (1945), Melinis repens (Willd.) Zizka (Poaceae)
1959	Rzedowski (1959), Salsola kali L. var. teniufolia Tausch (Amaranthaceae)
1980	Lot, Novelo & Cowan (1980), Phyllanthus fluitans Benth. ex Müll.Arg. (Euphorbiaceae)
1981	Espinosa-García (1981), Kickxia elatine (L.) Dumort. ssp. crinita (Mabille) Greuter (Plantaginaceae).; Polygonum convolvulus L. (Convolvulaceae)
1990	Rzedowski, & Calderón-de Rzedowski (1990), Several species of African origin
1993	Rzedowski (1993), Several Asteraceae species
1995	Vibrans (1995), Silene noctiflora L. (Caryophyllaceae)
1996	Vibrans (1996), Bellis perennis L., Guizotia abyssinica (Lf) Cass., Hypochaeris radicata L. (Asteraceae)
1997	Van Devender, Felger, Búrquez (1997), Several species in the Sonoran Desert
1998	Martin, Yetman, Fishbein, Jenkins, Van Devender & R. Wilson (1998), Several species in the Sonoran Desert
2001	Estrada & Yen (2001), Lespedeza cuneata (Dum.Cours.) G.Don (Fabaceae)
2003	Colmenero-Robles & Fernández-Nava (2003) Corchorus sp1 y sp2 (Tiliaceae)
2003	Rzedowski, Vibrans & G. Calderón-de Rzedowski (2003), Senecio inaequidens DC. (Asteraceae)
2003	Vibrans (2003) , Several species of Brassicaceae.
2005	Carranza-González (2005), Convolvulus crenatifolius Ruiz & Pavón (Convolvulaceae)
2005	Hanan-Alipi, Mondragón-Pichardo & Vibrans (2005), Ranunculus sardous Crantz. (Ranunculaceae)
2005	Rzedowski & Calderón-de Rzedowski (2005), Crepis capillaris Wallr. (Asteraceae).
2007	Van Devender & Reina (2007) . Sonoran Noteworthy Records, several species.
2008	Martínez, Mora-Olivo & Daniel (2008) , Hygrophila polysperma Anderson (Acanthaceae),
2008	Vibrans & Hanan-Alipi (2008), Polygonum nepalense Meisn. (Polygonaceae).
2009	Dimmitt, M. A., & T. R. Van Devender (2009), Brassica tournefortii Gouan. (Brassicaceae)
2010	Williams (2010) , twenty four exotic species not reported by Villaseñor and Espinosa-García (2004)
2013	Sánchez-Ken, G., J., Cerros-Tlatilpa, & Vibrans (2013) , Themeda quadrivalvis (L.) Kuntze (Poaceae)
2014	Mora-Olivo and Sánchez-Del Pino (2014) , Alternanthera philoxeroides Griseb. (Amaranthaceae)
2014	Vibrans, García-Moya, Clayton & Sánchez-Ken (2014), Hyparrhenia variabilis (L.) Stapf. and Hyparrhenia cymbaria Stapf. (Poaceae).
2015	Hinojosa-Espinosa & Villaseñor (2015), Arctotheca prostrata (Salisb.) Britten (Asteraceae).

 

Other important sources of new non-native species detection are the papers dealing with floristics that distinguish native and non-native species. There are floristic accounts concerned exclusively with non-native species ( Garcillán, de la Luz, Rebman, & Delgadillo, 2013; González-Elizondo, González-Elizondo, Tena-Flores, López-Enriquez, & Bacon, 2009; León-de la Luz, Domínguez, & Domínguez, 2009; Serrano-Cárdenas, Balderas-Aguilar, & Pelz-Marín, 2009; Villaseñor et al., 2012 ). An increasing number of floristic studies in specific ecosystems or regions have contributed to the knowledge of the distribution of non-native species. For specific ecosystems or landscapes: cities and surrounding areas ( Alfaro-Rodríguez & Arriaga, 2009; Corral-Díaz & Pelayo, 2009; Díaz-Betancourt, 1999; Martínez-de la Cruz et al., 2015; Vibrans, 1998 ); agroecosystems ( Martínez-Díaz & Jiménez-León, 2009; Sánchez-Blanco & Guevara-Féfer, 2013 ); pastures or grazing lands ( Gómez-Sánchez, Suárez-Martínez, & Martínez-Montes, 2011; Harker, García-Rubio, & Riojas-López, 2008; Lira-Noriega, Guevara, Laborde, & Sánchez-Ríos, 2007 ); wetlands ( Lot, 2012; Mora-Olivo, Villaseñor, & Martínez, 2013 ); savanna ( Ortiz-Díaz, Tun-Garrido, Arnelas-Seco, & García-Gil, 2014 ); and cloud forest and their edges ( López-Pérez, Tejero-Diez, Torres-Díaz, & Luna-Vega, 2011 ).

Some recent floristic accounts from regions of Nuevo León ( Guzmán-Lucio et al., 2013) and Guerrero ( Morales-Saldaña, Martínez-Ambriz, & Valencia, 2015 ), exemplify the increasing awarenes about the importance of non-native species among botanists and ecologists. A similar phenomenon is occurring with taxonomists, reviewing genera with native and non-native species ( Martínez-Bernal, Duno-de Stefano, & Lorena-Can, 2011; Saarela, Peterson, & Valdes-Reyna, 2014; Sánchez-del Pino, Espadas, & Pool, 2013 ).

The question of how many undetected non-native species are to be discovered in Mexico, remains to be answered after further floristic exploration and an implementation of an early detection and rapid response program operated by personnel familiarized with the local floras. However, a positive and significant correlation between native and non-native weed richness, and between non-weed native species and native weed richness has been found ( Espinosa-García, Villaseñor, & Vibrans, 2004b; Villaseñor, 2013 ). The estimated number of weeds in Mexico in 2012 was 683 introduced and 2,523 native species ( Villaseñor, 2013 ). Mexico has 23,314 documented species of flowering plants although this number could reach 29,000 ( Villaseñor, 2016 ). Considering that the non-native species represent between 2.6 and 10.3 (mean = 5.2 + 1.75%) of the Mexican States’ flora (data calculated from Villaseñor & Espinosa-García, 2004 ), and that the actual estimates of native plus non-native flora is between 24,014 and 24,064, we should expect to have approximately 1,260 non-native weed species (in the range between 834 and 1676). Thus, between 134 and 976 non-native weed species may yet to be documented in Mexico or are expected to arrive.

The estimates on the number of naturalized species that become invasive pests vary from 10% ( Williamson & Fitter, 1996), 12% ( Caley, Groves, & Barker, 2008 ) to 15–30% (Rejmánek & Randall, 2004 ). Thus, assuming that 20% ( Villaseñor & Espinosa-García, 2004 ) of the 700–750 non-native weeds in Mexico have naturalized (560–600), then an estimated number of invasive pest species in Mexico would be between 56 and 180. From the results of this review and our personal experience, we can clearly detect 37 highly problematic species, which need to be contained or have their negative effects mitigated ( Table 3 ). This list includes 8 invasive weeds that were identified formerly ( de Ita, Torres, Calderón, Luna, & Peralta, 1992 ). In a previous work, 33 invasive or invasive plant pests of high priority for Mexico were identified by a panel of scientists, NGOs’ personnel and government officials ( Aguilar et al., 2008 ); many of these species were not yet present in Mexico or some had been detected recently. Thus, the list of Table 3 and that of Aguilar et al. (2008) show little agreement. In a very recent contribution, Vibrans (2016) mentioned a number of highly problematic species that probably should be added to those in Table 3: Asphodelus fistulosus L., Canna indica L., Cyperus papyrus L., Dactyloctenium aegyptium (L.) Willd., Digitaria sanguinalis (L.) Scop., Digitaria velutina (Forsk.) Beauv., Eragrostis curvula (Schrader) Ness, Hyparrhenia hirta (L.) Stapf, Leonotis nepetifolia and Ricinus communis. Vibrans mentioned other non-native species that may be problematic in reduced areas, and others with widespread distribution but without evidence of causing environmental or economic damage. The UNIBIO survey of the biological invasions of plants ( http://www.unibio.unam.mx/invasoras/ ) listed 700 species of introduced plants, out of which 226 were classified as invasive, a greater number than the upper estimate obtained from the literature reviewed. The invasive species attributed high (133) and extreme invasiveness (7) represents 62% of the UNIBIOS’ invasive species pool. UNIBIO’s page, however, does not explain how the invasive category was assigned by the 67 floristic experts consulted to build the database because such category should be assigned according to their definition: “Una especie invasora es aquella que, como consecuencia de las actividades humanas, se ha expandido fuera de su rango de distribución natural, ha aumentado su densidad dentro de comunidades naturales de especies nativas y/o tiene impactos negativos en la biodiversidad de dichas comunidades” (an invasive species is one that, as a result of human activities, has expanded outside its natural range, has increased its density within natural communities of native species and/or has negative impacts on the biodiversity of these communities).

Table 3

Preliminary list of major invasive species detected in Mexico. The list was obtained from the results of this review and the authors’ experience. The suggested management options were determined based on the distribution extent: EDRR (early detection and rapid response) for incipient colonization of new ranges; local eradication for early stages of colonization; containment for non-eradicable species well established in an area but absent in other susceptible areas; mitigation for non-eradicable species occupying all the susceptible areas in the new range.

Family	Scientific name	Introduction mode	Management options
Amaranthaceae	Althernanthera phyloxeroides	Accidental introduction	EDRR, Containment
Amaranthaceae	Atriplex spp	Forage escapee	Containment
Amaranthaceae	Kochia scoparia	Forage escapee	Mitigation
Amaranthaceae	Salsola tragus	Forage escapee	Mitigation
Apocinaceae	Cryptostegia grandiflora	Ornamental escapee	Containment, Local eradication
Apocynaceae	Vinca major	Ornamental escapee	Containment
Araceae	Zantedeschia aethiopica	Ornamental escapee	Containment, Local eradication
Asteraceae	Centaurea melitensis	Accidental introduction	Containment, Local eradication
Asteraceae	Senecio inaequidens	Accidental introduction	Containment, Mitigation
Asteraceae	Taraxacum officinale	Accidental introduction	Mitigation
Brassicaceae	Brassica tournefortii	Accidental introduction	Containment
Casuarinaceae	Casuarina equisetifolia	Ornamental escapee	Containment, Local eradication
Convolvulaceae	Convolvulus arvensis	Accidental introduction	Mitigation, Biological control
Cyperaceae	Cyperus esculentus	Accidental introduction?	Mitigation, Biological control
Poaceae	Arundo donax	Utilitarian introduction	Containment, Local eradication, Biological control
Poaceae	Avena fatua	Accidental introduction	Mitigation, Biological control
Poaceae	Brachiaria mutica	Forage escapee	Mitigation
Poaceae	Bromus rubens	Accidental introduction	Containment, Mitigation
Poaceae	Cynodon dactylon	Forage escapee	Mitigation, Biological control
Poaceae	Digitaria decumbens	Forage escapee	Mitigation
Poaceae	Echinochloa crusgalli	Accidental introduction	Mitigation, Biological control
Poaceae	Echinochloa pyramidalis	Forage escapee	Mitigation, Cultural control
Poaceae	Hyparrhenia cymbaria	Accidental introduction	Eradication, Containment
Poaceae	Hyparrhenia rufa	Forage escapee	Mitigation
Poaceae	Hyparrhenia variabilis	Accidental introduction	Eradication, Containment
Poaceae	Megathirsus maximus	Forage escapee	Mitigation
Poaceae	Melinis repens	Forage escapee	Mitigation, Cultural control
Poaceae	Pennisetum ciliaris	Forage escapee	Containment, Mitigation
Poaceae	Pennisetum clandestinum	Ornamental and forage escapee	Mitigation
Poaceae	Phalaris minor	Accidental introduction	Mitigation, Containment for herbicide resistant varieties
Poaceae	Rottboellia cochinchinensis	Accidental introduction	Containment, Mitigation, Biological control
Poaceae	Schismus barbatus	Accidental introduction	Containment, Mitigation, Biological control
Poaceae	Sorghum halepense	Accidental introduction?	Mitigation, Biological control
Poaceae	Themeda quadrivalvis	Accidental introduction	Eradication, Containment
Polygonaceae	Polygonum convolvulus	Accidental introduction	Eradication, Containment
Pontederiaceae	Eichhornia crassipes	Ornamental escapee	Containment, Mitigation, Biological control
Tamaricaceae	Tamarix chinensis	Ornamental escapee	Containment, Local eradication

 

Aside of the important divergences of UNIBIO’s definition with the commonly accepted definitions in scientific literature (e.g. Richardson et al., 2000) or in official publications (CDB, 2009; DOF, 2015 ), the change in density should be determined by periodical observations of the same site. Also, the negative impacts should be documented. Since no indications of the qualification or quantification procedures for damage and density change are provided, the invasive and degree of invasiveness categorizations should be taken with caution.

In Mexico there is a small number of introduced species that are causing serious damage to agricultural and livestock systems and other ecosystems. This is the case of the Sonoran agricultural area where most of the problematic weeds were introduced purposely as forage or ornamental (Martínez-Díaz & Jiménez-León, 2009). These are grasses like buffelgrass ( Cenchrus ciliaris L.), rose Natal grass (M. repens [=Rhynchelytrum repens (Willd.) C. E. Hubb.]), kikuyu grass ( Pennisetum clandestinum Hochst. ex Chiov.), Johnson grass ( Sorghum halepense (L.) Pers.), and those causing the “Africanization of Americas tropics” ( Parsons, 1972 ). Amaranthaceae introduced for forage are some salt-bush species Atriplex spp., fireweed or burning bush Kochia scoparia (L.) Schrad., and tumbleweed Salsola tragus L. Notorious ornamentals that had escaped and naturalized are water hyacinth ( E. crassipes), white arum hyacinth (Zantedeschia aethiopica (L.) Spreng.), vinca or periwinkle ( Vinca major L.) and the rubber vine (Cryptostegia grandiflora R. Br.) ( Pérez-Panduro, 1998; Rodríguez-Estrella, Pérez-Navarro, Granados, & Rivera, 2010 ). In a publication on agricultural weeds of northern Mexico and the Mexican plateau ( de Ita et al., 1992 ), 10 of 22 species cited are non-native ( A. fatua, Chenopodium album L. Bosc ex Moq., Convolvulus arvensis L., Cynodon dactylon (L.) Pers., Cyperus esculentus L., Echinochloa crusgalli (L.) P. Beauv., Phalaris minor Retz., Rumex crispus L., S. halepense, and Taraxacum officinale G. H. Weber ex Wigg.).

Distribution

Most introduced species have a restricted distribution in Mexico compared with native weeds; moreover, the distribution pattern of introduced weeds at the state scale is similar to that of native non-weeds, that is, most species are reported from 1–2 states ( Espinosa-García, Villaseñor, & Vibrans, 2004a ). This pattern has to be confirmed because the number of botanists interested in non-native weeds is limited. However, we pose the hypothesis that most introduced species with wide distribution are a problem in cultivated or natural areas such as those species mentioned in the previous section.

Biogeographical studies of the Mexican flora including non-native weeds are few ( Luna-Vega, 2008 ). Most temperate non-native species come from Eurasia and the Mediterranean region, whereas most tropical ones come from Africa, via South America ( Rzedowski, 1993; Rzedowski & Calderón-de Rzedowski, 1990; Villaseñor & Espinosa-García, 2004 ). The diversity of native and introduced weed species is closely correlated with the diversity of native non-weed species ( r = 0.7–0.9) ( Espinosa-García et al., 2004b; Villaseñor, 2013 ). This agrees with the global pattern in which “the rich get richer” that implies that the regions with more native diversity have more introduced species ( Stohlgren, Barnett, & Kartesz, 2003 ). However, the distribution of the invasive pest species is probably not strongly related to native plant biodiversity but with the invasibility of the territory and the propagule pressure for each region ( del Val et al., 2015 ). The potential distribution patterns of the invasive pest species according to their invasivity degree are still to be described in order to sustainably manage the areas threatened by these species.

Studies on the current or potential distribution of specific non-native species in Mexico range from distribution patterns at the local scale, for example a university campus ( Zavala-Hurtado, Portilla-Gutiérrez, Ayala-Fernández, & Bravo-Rivera, 2003 ), to the national scale, modeling the potential distribution of the introduced Asteraceae in Mexico and the actual and potential distribution of S. molle ( Ramírez-Albores, Bustamante, & Badano, 2016; Villaseñor et al., 2012 ). The distribution of most non-native species has been recorded at the state scale ( Espinosa-García et al., 2009; Villaseñor & Espinosa-García, 1998 ), but few detailed actual and potential distributions of non-native species are know: buffel grass ( C. ciliaris ) in Sonora and the Baja California Peninsula ( Arriaga, Castellanos, Moreno, & Alarcón, 2004 ); testing the effectiveness of various potential distribution models with Brassica tournefortii Gouan and Schismus arabicus Nees in the Sonoran Desert ( Sánchez-Flores, 2007; Sánchez-Flores, Rodríguez-Gallegos, & Yool, 2008 ); Hypochaeris radicata L. actual distribution in Mexico city ( Hinojosa-Espinosa & Cruz-Durán, 2008 ); Arundo donax L., tracing its multiple introductions and identifying the origin of the genotypes that invaded the Río Bravo Basin ( Tarin et al., 2013); and Atriplex semibaccata R. Br., B. tournefortii, Bromus rubens L., Centaurea melitensis L., C. dactylon, S. tragus, Schismus barbatus, and Tamarix chinensis Lour (=T. ramossisima Ledeb.), in Baja California ( Palma-Ordaz & Delgadillo-Rodríguez, 2014 ). A special mention is for the Villaseñor et al. (2012) comprehensive work for the potential distribution for 30 of the 61 species of the non-native Asteraceae in the whole country performed with ecological niche models using MaxEnt.

Actual and potential distribution studies are very important for management prioritization, early detection, eradication, containment and mitigation. The knowledge on actual or potential distribution of non-native weeds in Mexico is fragmented and disarticulated with decision makers. However, the completion of the analysis of the distribution of non-native weeds and its linkage to decision makers is included in the National Strategy for Invasive Species ( Comité Asesor Nacional sobre Especies Invasoras, 2010 ) and in the recent National Biodiversity Strategy for Mexico ( Conabio, 2016 ). A major effort is needed to promote these studies with the co-participation of researchers and decision makers.

Ecology

Ecological publications cover a wide range of topics, often focusing on one aspect of a single species, with the notable exception of the publications of Patricia Moreno-Casasola and her research group, focusing on the invasion of a marsh by Echinochloa pyramidalis (Lam.) Hitch. & Chase. They have documented the invasion ( Castillo & Moreno-Casasola, 1996 ), explored the impact of cattle ranching practices on the invasion ( Travieso-Bello, Moreno-Casasola, & Campos, 2005 ), and studied the relationships of hydroperiod and water physicochemical properties with competition among hydrophytes in the marsh ( López-Rosas & Moreno-Casasola, 2012; Peralta-Pelaez, Moreno-Casasola, & López-Rosas, 2014 ). This group used these studies and others in restoration ecology ( López-Rosas, Moreno-Casasola, & Espejel-González, 2015 ) to reverse the invasion by E. pyramidalis with partial success and they continue the restoration efforts (see the management section). Focusing in one ecological aspect of a single invasive species is frequent in Mexican ecologists: reproductive ecology of N. glauca (Hernández, 1981); demography of E. crassipes (Niño-Sulkowska & Lot, 1983 ); ecophysiology of gas exchange of C. ciliaris ( De la Barrera & Castellanos, 2007 ); oil contamination effects on M. repens and C. ciliaris ( Reynoso-Cuevas, Gallegos-Martínez, Cruz-Sosa, & Gutiérrez-Rojas, 2008 ); population genetics of ruderal and cultivated populations of C. ciliaris ( Gutiérrez-Ozuna, Eguiarte, & Molina-Freaner, 2009 ); fate of M. repens in the soil seed bank of Neo-Tropical pastures ( Maza-Villalobos, Lemus-Herrera, & Martínez-Ramos, 2011 ); fitness of M. repens growing under different regimes of soil humidity ( Díaz-Romo et al., 2012 ); reproductive ecology of the orchid Oncidium poikilostalix (Kränzl.) M.W. Chase & N.H. Williams ( García-González, Damon, Iturbide, & Olalde-Portugal, 2013 ), and invasion by clonal spread of Kalanchoe delagoensis Eckl. & Zeyh. ( Guerra-García, Golubov, & Mandujano, 2015 ). Competition between herbicide-resistant and herbicide-susceptible accessions of P. minor has been studied (Torres-García et al., 2015 ) as well as the herbicide resistance traits presented by this grass in wheat fields ( Cruz-Hipólito, Domínguez-Valenzuela, Osuna, & De Prado, 2012; García-Franco et al., 2014 ).

Other authors have focused on communities or groups of invasive species: for example, how changes in the hydrological regime and salinity have caused T. chinensis invasion of the Colorado River delta and how the reversal of those changes allow the regeneration of the native plant communities ( Glenn et al., 1998; Nagler et al., 2005 ); life-history diversity of native and non-native species in heterogeneous vegetation ( Pérez-García, Meave, Villaseñor, Gallardo-Cruz, & Lebrija-Trejos, 2010 ); incidence of non-native weed species along an altitudinal gradient ( Sánchez-González & López-Mata, 2005 ); plant richness analysis of areas where non-native grasses are abundant ( Cano-Santana, Castillo-Arguero, Martínez-Orea, & Juárez-Orozco, 2008 ); incidence of non-native species in small patches in fragmented forests ( Arroyo-Rodríguez, Pineda, Escobar, & Benitez-Malvido, 2009 ); population genetics of Sinorhizobium spp. mutualists isolated from Medicago spp. ( Silva, Kan, & Martínez-Romero, 2007 ); and seed bank ecology of agricultural fields in the tropical dry forest ( Meave, Flores-Rodríguez, Pérez-García, & Romero-Romero, 2012 ). Few authors have focused on non-native weed ecology either by studying the combination of factors influencing non-native richness ( Espinosa-García et al., 2004b ) or by combining several ecological variables to build a model to identify risk areas in Mexico ( del Val et al., 2015). Santibañez-Andrade, Castillo-Arguero, and Martínez-Orea (2015) determined that the importance index of weeds, native and non-native, is an important aid to asses the conservation status of temperate forests.

There is a group of studies testing hypotheses on invasiveness by comparing populations of Mexican native species that are invasive elsewhere in the world such as Ageratina adenophora (Spreng.) King & H.Rob. and Chromolaena odorata (L.) R.M.King & H.Rob. For example, the EICA (Evolution of Increased Competitive Ability) hypothesis and the Novel Weapons hypothesis (NWH) were tested with both species ( Feng et al., 2009, 2011; Inderjit et al., 2011; Qin et al., 2013; Zheng et al., 2015 ). EICA postulates that change in resource allocation in invasive species produces high competitive ability, which in turn determines a successful invasion; the NWH postulates that invasive success is determined by biochemical weapons (allelopathy) of the invasive that are novel for the invaded range native plants. The comparison of native and invasive populations of A. adenophora and C. odorata made by the previously cited authors suggest that both increased competitive ability and the possession of novel weapons operate in the success of these species as invasives.

Research on the ecology of native species that are invasive elsewhere has also been published, such as the demography of Prosopis glandulosa Torr. (Golubov et al., 1999); bacterial symbionts of Mimosa spp. (Elliott et al., 2009 ) and the relationship of herbivory with terpenoid variability at local and regional scales for Mikania micrantha Kunth and the specialist insect herbivore Stolas punicea (Boheman, 1850) ( Bravo-Monzón, Ríos-Vásquez, Delgado-Lamas, & Espinosa-García, 2014, 2016 ).

Although the operative definition of invasive species conveys the introduction of the plant to a new country, i.e. an exotic or alien plant, there are cases where a native plant species is introduced to a new range within a country. These plants are called “translocated”, but others call them “invasives” in agreement with the Convention on Biological Diversity definition, as it is the case of the authors that contributed to the theory of ecological invasions. Ruellia nudiflora (Engelm. & A.Gray) Urb. is a native species in many states of Mexico, but not in Yucatan, where it behaves as invasive. Víctor Parra-Tabla and his research group have compared Yucatan’s native Ruellia species with R. nudiflora on germination, seedling survival, reproductive phenology and niche width ( Cervera & Parra-Tabla, 2009; Munguía-Rosas, Parra-Tabla, Ollerton, & Carlos Cervera, 2012; Vargas-Mendoza, Ortegon-Campos, Manufo-Zapata, Herrera, & Parra-Tabla, 2015 ). Roberto Lindig-Cisneros’ research group has worked with “translocated” or “invasive” Phragmites australis (Cav.) Trin. ex Steud., and Typha dominguensis Pers. in wetlands. Both species have a widespread original range, the former a neartic one and the later in the Americas, but these species colonize wetlands behaving like invasives displacing native species particularly after perturbations in the nutrient regime by eutrophication ( P. australis) or fire (T. dominguensis) ( Escutia-Lara & Lindig-Cisneros, 2012; López-Arcos, Gómez-Romero, Lindig-Cisneros, & Zedler, 2012 ). Another case of a translocated species is Stenocereus griseus (Haw.) Buxb., introduced as crop in a part of Oaxaca, but now becoming feral and apparently displacing Escontria chiotilla (F.A.C.Weber ex K.Schum.) Rose, in the wild ( Ramírez-Galindo, Barbosa-Martínez, & Ponce-de León, 2011 ).

We found publications in which native species are labeled as “native invasive” species Tithonia tubiformis (Jacq.) Cass. and T. rotundifolia (P. Mill.) S.F. Blake ( Tovar-Sánchez et al., 2012) and as invasive species, Ferocactus latispinus (Haw.) Britton & Rose and Viguiera dentata (Cav.) Spreng. ( Aquino-Soto, Zavala-Hurtado, Pérez-Moreno, & Camargo-Ricalde, 2012 ). In contrast with the possibly invasive or translocated species, in the Tithonia spp., F. latispinus and V. dentata cases there is no evidence of a condition of insularity (such as wetlands), peninsularity (such as Yucatán) or other physiographic traits that could function as barriers. Barriers are important in isolating the invasive species from their natural enemies; the release from natural enemies is supposed to be one of the main mechanisms that allow invasive species to become more competitive in the new range by reallocating to competition resources previously used for defense against natural enemies ( Moles et al., 2012 ). Thus, we suggest that the term “native invasive” is inadequate to qualify the mentioned Tithonia species or their hybrid in Mexico, and that F. latispinus and V. dentata should not be labeled as invasive in Puebla.

Economic and environmental impact of non-native weeds

There are numerous agricultural publications in Mexico, not included in this review, showing the negative effects of weeds on crops, either by causing severe harvest reduction by competition or as refuge for crop pests and pathogens. However, most of these studies are mainly at a small landowner scale without separating the effects of native vs. non-native weeds, and as far as we know, none quantifies the economic impact of weeds at a regional or national scale. A general review of the potential impacts caused by invasive plants impacts was briefly addressed by Aguirre-Muñoz and Mendoza-Alfaro (2009) , based mainly on the information of Espinosa-García et al. (2009) . Cost estimates of weed effects and control were presumed high ( Espinosa-García et al., 2009 ) by observing weed-associated losses in United States, where 34,660 million dollars was the combined cost (losses and control) of weeds in 2003 ( Pimentel et al., 2002; Pimentel, Zúñiga, & Morrison, 2005; Westbrooks, 1998 ). However, it is difficult to extrapolate costs due to the big differences in weed flora ( Espinosa-García et al., 2009 ) and the diversity of agricultural production models prevalent in both countries. Still, potential yield losses of 38–73% (average 52%) in corn produced in United States were estimated for a non-weed control condition ( Dille, Sikkema, Everman, Davis, & Burke, 2015 ); the magnitude of the loss is probably similar for conventional corn production in Mexico. Some invasive weeds are a big problem in Mexico. For example, Johnson grass ( S. halepense ) is a highly competitive perennial grass that aside from causing strong yield reductions in several crops in northern Mexico and the Bajío ( Gámez-González et al., 2002 ), also hosts Claviceps africana and the pepper huasteco geminivirus ( Garzón-Tiznado et al., 2002; Montes-Belmont, Flores-Moctezuma, & Nava-Juarez, 2013 ). Again, there is no national cost estimation for Johnson grass or any other weed, especially the invasive species mentioned here (see the section “Floristics and detection of new non-native species for Mexico)” except for the water hyacinth, E. crassipes (Pérez-Panduro, 1998 ). Four hundred and fourty one million dollars were the annual estimated losses in weed control and the direct and indirect effects caused by the water hyacinth (see Espinosa-García et al., 2009 ). Additional non-native weeds, such as Marrubium vulgare L., have been reported as hosts of the African cluster bug Agnoscelis puberula Spinola, 1837 ( Ortega-León, Thomas, & Soriano, 2006; Thomas, Eger, Jones, & Ortega-León, 2003 ). L. nepetifolia (L.) R. Br., formerly used as ornamental, is now a ruderal weed in almost all Mexico ( Villaseñor & Espinosa-García, 1998 ), and it is an important virus reservoir for phytopathogenic virus ( Piedra-Ibarra, de la Torre-Almaraz, Zúniga, Xoconostle-Cazares, & Ruiz-Medrano, 2005 ).

Aside from direct and indirect economic losses caused by non-indigenous weeds, it is very difficult to monetarily evaluate several collateral costs such as harmful effects on human health, water and soil pollution by herbicides, and disruption of ecosystem services ( Bejarano-González, 2002; Hansen et al., 2013 ). In the USA, chemical control for all pests cost $5,000 million dollars per year, meaning $20,000 in savings in crop yields ( Pimentel et al., 2005 ). Environmental pollution and human health costs are not included and there is no clear means of identifying or quantifying the additional cost.

Costs associated to non-native weed in Mexico must be significant considering the expenses in other countries, especially since ecological and human health problems related to pesticides are bigger and more expensive in third world countries ( Jeschke et al., 2014; Pimentel et al., 2002 ). In Mexico, 15,719 ton of herbicides were used in 1995 ( Inegi-Semarnap, 1999); 4,472 tons of the most popular herbicides (2,4-D, paraquat, atrazine, picloram, and glyphosate) were used in 1999. Sales figures for such herbicides in 1999 (except Atrazine) were 537 million MXP ( Bejarano-González, 2002 ). It is impossible to calculate the share linked to introduced species; 22% of weeds are introduced, but almost half of the 24 species cited as problematic for intensive agriculture in the Mexican plateau and northern Mexico are introduced ( de Ita et al., 1992 ). In addition, agrochemical companies jealously guard their sales figures, making it difficult to estimate the actual weed control costs related directly to productivity and those indirectly related with negative effects on ecosystem services, human health and soil and water contamination.

Quantification of environmental and economic impacts becomes very difficult when the invasive species has an important economic use. This is the case of invasive African grasses introduced as forage such as E. pyramidalis (German grass), a forage plant introduced in the Mexican tropics for cattle raising that became invasive in marshes ( López-Rosas, Moreno-Casasola, & Mendelssohn, 2005, 2006 ), C. ciliaris (buffel grass) that has been sown in Sonora and other northern Mexican states for cattle raising ( Durán-Puga et al., 2011; Marshall, Friedel, van Klinken, & Grice, 2011; Quero-Carrillo, Enríquez-Quiroz, Morales-Nieto, & Miranda-Jiménez, 2010; Ramírez, Haenlein, García-Castillo, & Núñez-González, 2004 ). However, this grass became wild and, being prone to fire, has caused the elimination of non-fire adapted vegetation ( Búrquez-Montijo, Miller, & Martínez-Yrizar, 2002; Franklin et al., 2006; Van Devender, Espinosa-García, Harper-Lore, & Hubbard, 2009 ). The grasses identified by Parsons (1972) as those causing the africanization of the Americas tropics: Megathirsus maximus (Jacq.) B.K. Simon & S.W.L. Jacobs (Guinea grass), Urochloa mutica (Forssk.) T.Q. Nguyen (= Brachiaria mutica; Pará grass), Melinis minutiflora P. Beauv. (molasses grass.), Hyparrhenia rufa (Nees) Stapf (jaraguá), P. clandestinum Hochst. ex Chiov. (Kikuyu grass), Digitaria eriantha Steud. (=D. decumbens Stent; Pangola grass), have also become invasive. The effect of grasses, with little or no forage value, has been documented in Mexico; they affect local biodiversity by direct displacement or interference with seedling establishment; for example, M. repens in grasslands in Durango ( Herrera-Arrieta, Pámanes-García, Herrera-Corral, Chairez-Hemandez, & Cortés-Ortiz, 2011 ), several invasive grasses in humid montane forests ( Ortega-Pieck, López-Barrera, Ramírez-Marcial, & García-Franco, 2011 ), and E. pyramidalis in a tropical freshwater marsh (López-Rosas et al., 2006 ). The removal of some of those grasses in abandoned tropical pastures allows the establishment and growth of native trees ( Román-Dañobeytia et al., 2012 ).

In agricultural systems, invasive grasses affect crop growth, for example, C. dactylon, S. halepense ( Gámez-González et al., 2002 ), and Rottboellia cochinchinensis (Lour.) Clayton ( Contreras-Ramos et al., 2013; Tucuch-Cauich, Orona-Castro, Almeyda-León, & Aguirre-Uribe, 2013 ). In Oasis, the invasive vine C. grandiflora , makes the habitat unsuitable for birds and reptiles ( Rodríguez-Estrella et al., 2010 ). The environmental effects of E. crassipes are mixed, as it may harbor Anopheles albimannus C. R. G. Wiedemann, 1820, a malarial vector ( Savage, Rejmankova, Arredondo-Jiménez, Roberts, & Rodríguez, 1990 ), some free living amoebae pathogenic to humans ( Ramírez, Robles, & Martínez, 2010 ), reduce water quality ( Gutiérrez, Huerto, Saldana, & Arreguín, 1996; Lind & Davalos-Lind, 2002 ), or become inhospitable to small migratory birds ( Villamagna, Murphy, & Karpanty, 2012 ), but E. crassipes also may harbor a great diversity of invertebrates and function as preferred foraging habitat for coots ( Hernández et al., 2015; Rocha-Ramírez, Ramírez-Rojas, & Chávez-López, 2007; Rocha-Ramírez, Robles-Valderrama, & Ramírez-Flores, 2014; Román-Contreras, Rocha-Ramírez, & Cházaro-Olvera, 2008; Villamagna, Murphy, & Trauger, 2010 ). Water hyacinth also removes heavy metals and insecticides from water (see management and use section).

Environmental impacts are difficult to measure and do not necessarily increase proportionally with invasive species biomass ( Jeschke et al., 2014 ), however, a new classification scheme for invasive species environmental impacts ( Blackburn et al., 2014 ) could be useful to evaluate invasive impact for Mexican conditions. Considering that many non-native species never become invasive, and that even when they are invasive some of them cause environmental change directly (drivers) while others just prosper in an already changed one (passengers) ( MacDougall & Turkington, 2005 ), it is imperative to develop or adapt a classification scheme suited for Mexico that distinguish the actual or potential ecological role of the evaluated species in heterogeneous regions. Apart from the expensive cost of losing ecosystem services (water retention, recreation, pollination, pest control and soil conservation), native biodiversity is also impacted. For example, loss of native vegetation, directly or through fire, has been documented for buffelgrass and Sahara mustard ( B. tournefortii ), invasive species occupying huge regions in northwestern Mexico ( Búrquez-Montijo et al., 2002; Dimmitt & Van Devender, 2009 ).

Summarizing, the negative effects of invasive species on the environment, productive systems and human health are important and diverse, but complete damage quantification for most invasive species is lacking, and it is imperative to allocate economic and human resources to prevent and mitigate the noxious effects of these non-native species.

Management of non-native weeds

Proper management of non-native weeds includes prevention, early detection, eradication, containment and mitigation. All these tasks should be integrated in a National weed management strategy able to deal with native and non-native weeds at various spatial and time scales ( Espinosa-García & Vibrans, 2009 ). The national strategy is only viable if all the stakeholders, individuals and institutions are well aware of the needs for weed control and the effects of weed invasions ( Espinosa-García, 2009 ). In spite of having a National Invasive Species Strategy ( Comité Asesor Nacional sobre Especies Invasoras, 2010 ), the individualistic weed management model is still prevalent among producers and the articulation among government institutions, producers and academia is still poor, but it has some improvement since 2008 ( Espinosa-García, 2009 ). For example, prior to 2008, there was not a single eradication campaign for invasive weeds in spite of published reports of quarantine weeds growing in Mexico such as Polygonum convolvulus (Espinosa-García, 1981) or Rotttboellia conchinchinensis ( Esqueda-Esquivel, 2000; Medina-Pitalúa & Domínguez-Valenzuela, 2001 ). Then, after Juan Carlos Delgado and his team of the “Comité Estatal de Sanidad Vegetal de Guanajuato” detected several P. convolvulus infestations in wheat fields in Guanajuato ( Delgado-Castillo, 2010 ), an official eradication campaign, promoted by Delgado, was started, resulting in a very strong reduction of the weed in the infested fields ( Vibrans & Delgado, 2010 ). Eradication campaigns have followed since in several states for P. convolvulus, Cuscuta indecora Choisy, R. cochinchinensis and Themeda quadrivalvis , although in many cases eradication was not achieved and in some states the quarantined weeds have increased their density (see internet reports of “Campañas contra Malezas Cuarentenarias” or “Campañas contra malezas reglamentadas” for Mexico or for the “Comités Estatales de Sanidad Vegetal”, for example h t t p & # 5 8 ; & # 4 7 ; & # 4 7 ; w w w .gob.mx/senasica/acciones-y-programas/malezas-reglamentadas ).

Advances in Mexico on general management issues have been concentrated in diagnostic studies involving the identification of threatening species ( Aguilar et al., 2008; Peña-Jiménez & Neyra-González, 1998; Semarnat, 2016 ); biodiversity estimates, distribution and possible impacts of non-native weeds for Mexico ( Espinosa-García et al., 2009 ); policies on invasives (Arriaga, 2009 ); and management strategies and cooperation at national and international scales ( Espinosa-García & Van Devender, 2009; Espinosa-García & Vibrans, 2009 ). There are also methodological proposals exemplified with taxonomic groups, specific regions or countries or invasive species, mainly for species prioritization for management actions ( Sánchez-Blanco, Sánchez-Blanco, Mario Sousa, & Espinosa-García, 2012 ), distribution modeling ( Sánchez-Flores, 2007; Sánchez-Flores et al., 2008 ), and infestation monitoring modeling ( Sonnentag et al., 2011).

Control and use of non-native weeds

Weed control generally involves drastic abundance reduction or elimination from a generally small area, under an individualistic weed management model that promotes the misuse or abuse of herbicides and poor control of noxious or invasive weeds ( Espinosa-García & Vibrans, 2009 ). The prevalent weed control mode has been chemical (not covered in this review), although weed herbicide resistance and the negative effects on non-target species have fostered control efforts by biological, mechanical, solarization ( Lira-Saldívar et al., 2004 ) or integrated control, mainly for some invasive weeds.

Most publications on weed management deal with biological control of E. crassipes, C. arvensis, S. halepense, A. donax (Goolsby et al., 2011) and Althernanthera phyloxeroides (Mart.) Griseb. ( Lara-Villalón, Mora-Olivo, Sánchez-Ramos, & Martínez-Ávalos, 2014 ). Water hyacinth is the most studied invasive weed, testing insects ( Aguilar, Camarena, Center, & Bojórquez, 2003; Martínez-Jiménez, Gutiérrez-López, Huerto-Delgadillo, & Ruiz-Franco, 2001; Martínez-Morales, Estrada-Venegas, Equihua-Martínez, & Valdez-Carrasco, 2014; Pérez-Panduro, 1998 ), fungi ( Martínez-Jiménez & Charudattan, 1998; Martínez-Jiménez & Gutiérrez-López, 2001; Martínez-Jiménez, Gutiérrez-López, et al., 2001; Martínez-Jiménez, Brown et al., 2001 ) or both kinds of natural enemies for control purposes ( Martínez-Jiménez & Gómez-Balandra, 2007 ). Even with some successes in biological control, water hyacinth still is one of the most troublesome invasive species that is mostly managed with mechanical control ( Mangas-Ramírez & Elías-Gutiérrez, 2004 ) that many times reduces temporarily water hyacinth abundance, making the removal of this plant a permanent activity or business for those that own and operate the machinery needed for this task. Chemical control has been applied also, but concerns about herbicide toxicity in water have limited this kind of management (see Santibañez-Aguilar, Ponce-Ortega, González-Campos, Serna-González, & El Hawagi, 2013 ). Moreover, the seed bank of E. crassipes in the sediments provides new recruits when successful removal of the floating plants has been achieved ( Santibañez-Aguilar et al., 2013 ). Some attempts or proposals have been made to use water hyacinth as forage, mulch or as a phytoremediation agent to remove heavy metals or organophosphorus and organochlorine pesticides from water ( Fileto-Perez et al., 2015; Mercado-Borrayo, Heydrich, Pérez, Quiroz, & Hill, 2015; Rodríguez, Avila-Pérez, & Barceló-Quintal, 1998; Santibañez-Aguilar et al., 2013; Tejeda, Zarazua, Avila-Pérez, Carapia-Morales, & Martínez, 2010 ). In spite of calls for integrated management of water hyacinth ( Gutiérrez et al., 1996 ) and many proposed uses for this plant, the problems caused by E. crassipes continue. A recent proposal for biorefining networks to process E. crassipes biomass for profit might contribute strongly to prevent or mitigate water hyacinth damage to water bodies ( Santibañez-Aguilar et al., 2013 ), but still that proposal has yet to become a reality. The theme of finding uses or beneficial environmental effects for invasive plants has also been repeated for tamarisk ( Tamarix ramosissima Ledeb.) ( MacGregor-Fors, Ortega-Álvarez, Barrera-Guzman, Sevillano, & del Val, 2013 ), field bindweed, Johnson grass, natal grass and other escaped forage grasses (see section ahead). Still a cost-benefit analysis of the effects of these invasives could show that the negative effects will probably outweigh the positive ones.

Chemical control of field bindweed or correhuela ( C. arvensis ), a highly problematic weed, has been frequently studied (e.g. Tamayo-Esquer & Gaillardon, 1989); also cultural control (Robles et al., 2006 ) and biological control with mites ( Rodríguez-Navarro, Flores-Macías, & Torres-Martínez, 2008; Rodríguez-Navarro, Rodríguez-Morell, Alemán-Martínez, Flores-Macías, & Torres-Martínez, 2011; Rodríguez-Navarro, Torres-Martínez, & Olivares-Orozco, 2004 ) have been studied, but as far as we know, the biological control for this weed has not been generalized. The use of C. arvensis also has been explored for phytoremediation by heavy metal accumulation ( Cruz-Jiménez et al., 2005; Gardea-Torresdey, Peralta-Videa, Montes, de la Rosa, & Corral-Díaz, 2004; Montes, Peralta-Videa, Parsons, Corral Díaz, & Gardea-Torresdey, 2013; Montes-Holguin et al., 2006 ). A similar pattern of studies as that found with correhuela is the one with Johnson grass ( S. halepense ) with studies on chemical control ( Esqueda-Esquivel, Uresti-Durán, & Hernández-Aragón, 2015; Magallanes et al., 1986; Vera-Núñez, Grageda-Cabrera, Altamirano-Hernández, & Peña-Cabriales, 2010 ); biological control ( Iracheta-Cárdenas, Galan-Wong, & Pereyra-Alferez, 1995; Martínez-Mendoza et al., 2012 ); and use as forage ( Castro-González, Alayon-Gamboa, Ayala-Burgos, & Ramírez-Aviles, 2008; Gutiérrez et al., 2008; Ramírez-Vera et al., 2012 ).

1. minutiflora is so widely distributed that novel attempts for its use have been evaluated: first as repellent for Rhipicephalus microplus (Canestrini, 1888) (= Boophilus microplus ), a cattle tick pest in the tropics ( Fernández-Ruvalcaba et al., 2003; Fernández-Ruvalcaba, Preciado-de la Torre, Cruz-Vázquez, & García-Vázquez, 2004; Muro-Castrejón, Cruz-Vázquez, Fernández-Ruvalcaba, & Torres, 2004 ), and later again as forage ( Durán-Puga et al., 2011; Murillo-Ortiz, Mellado-Bosque, Herrera-Torres, Reyes-Estrada, & Carrete-Carreon, 2014; Ramírez et al., 2009 ).

As Mexico is within the area of origin for important invasive plants elsewhere, we found five publications prospecting for natural enemies of invasive species mainly in Australia: Sida acuta Burm. f. and Sida rhombifolia L. ( Gillett, Harley, Kassulke, & Miranda, 1991 ); Mimosa pigra L. ( Heard et al., 2010; Heard, Mira, Fichera, & Segura, 2012 ); Parkinsonia aculeata L. ( Brown, Segura, Santiago-Jiménez, Rota, & Heard, 2011 ); Lantana camara L. ( Manners, Palmer, Burgos, McCarthy, & Walter, 2011 ) and Jatropha gossypiifolia L. ( Heard, Dhileepan, Bebawi, Bell, & Segura, 2012 ). In adition, a neotropical nematode was detected as a promising biocontrol against native Melastomataceae: Clidemia hirta (L.) D.Don, Miconia calvescens DC., and Tibouchina herbacea (DC.) Cogn. (Oliveira et al., 2013).

Many non-native weeds naturalized long time ago are now used by Mexican ethnic groups as medicinal plants, for rituals, or emergency food ( Blancas, Casas, Pérez-Salicrup, Caballero, & Vega, 2013; Blancas et al., 2010; Blanckaert et al., 2007; Flores & Kantun-Balam, 1997; Sánchez-González, Granados-Sánchez, & Simón-Nabor, 2008 ). A special case is that of the pirú ( S. molle ), a tree naturalized long ago and widespread in the Mexican plateau, which has cultural and medicinal importance in Mexico ( Ramírez-Albores & Badano, 2013 ). The invasive label for the pirú is valid if the invasive definition is based on the formation of new populations 100 m or more away of the original population ( Richardson et al., 2000 ), but that label does not hold considering the requisite of proof of economic or environmental damage or threat ( CDB, 2009; DOF, 2015 ). Although allelopathic effects were suggested for pirú ( Anaya & Gómez-Pompa, 1971 ), and the tree is frequently found growing in several ecosystems, there is no evidence of local extirpations or extinctions caused by this tree. Perhaps we are witnessing a naturalization case more than an invasion by this non-native tree.

Research on management of invasive plants for restoration purposes

Although few papers have been published on the management of invasive plants for restoration purposes, a series of studies in a wetland invaded by E. pyramidalis is remarkable. These studies include description, damage evaluation, invasive dynamics and restoration methods ( López-Rosas & Moreno-Casasola, 2012; López-Rosas et al., 2006; Moreno-Casasola et al., 2016 ). Other restoration programs, particularly in the Humid Forests Biome and tropical dry forests, include invasive weeds removal (particularly grasses and ferns) to facilitate the establishment of desired plant species ( López-Barrera et al., 2016; Martínez-Garza, Osorio-Beristain, Alcalá-Martínez, Valenzuela-Galván, & Mariano, 2016; Román-Dañobeytia et al., 2012; Williams-Linera & Álvarez-Aquino, 2016 ). In the cases where the invasive species prospers only after the environment has been disturbed, i.e. passanger species ( MacDougall & Turkington, 2005 ), the restoration occurs after the disturbance factors are removed. For example, native trees return displacing T. chinensis in the Colorado River delta when the hidological and salinity regimes return to pre-invasion levels ( Nagler et al., 2005).

General overview of the scientific knowledge on non-native species

The National Strategy on Invasive Species for Mexico emphasizes that scientific information is imperative to achieve an adequate knowledge and management of plant invasions and non-native weed species (strategic transversal actions: knowledge and information). This review shows that there are significant advances in the scientific knowledge on non-native species across many topics, mainly the check-list of the species present in Mexico and their incidence at a state scale. There has also been a constant addition of previously undetected species to the checklist of non-native weeds in Mexico, but these contributions result from the activity of few researchers that divide their interests between invasive species and several other academic fields. Although this approach has yielded acceptable results, it should be complementary of a dedicated and permanent early detection program led by federal agencies in which botanists and the general public participate (e.g. Citizen Science, http://www.naturalista.mx/ ).

Very few studies on the detailed distribution, actual or potential, are available for invasive weeds, but none of them have been used to take preventive or management actions by policy or decision makers. The information on weed distribution is imperative for risk analysis and management, but it is lacking for most non-native weeds in Mexico. Similarly, the information on risk analysis to prevent the entrance of invasive species or to prioritize attention to the invasive species already present in Mexico is still incomplete and missing for most species present in the country. The knowledge of the impacts by non-native species on the environment, economy or human health, is necessary for risk analysis and prioritization of management. However, as seen in this review, this knowledge is limited to a few species, studied locally and has not been quantified at the regional or national scales, except for the water hyacinth ( Pérez-Panduro, 1998 ), although this quantification should be updated. A particularly difficult challenge is that of the control of the widely used invasive species that escape cultivation causing noxious effects, such as the grasses introduced for forage reviewed previously. Most of these grasses are very important for cattle rising, and the control measures are strongly opposed by ranchers. For example, there are numerous studies on the distribution, ecology and negative effects of buffel grass ( C. ciliaris ), but the areas planted with this grass have not diminished. Furthermore, the Mexican official research institution for agriculture and cattle rising (INIFAP) promotes C. ciliaris cultivation by developing new buffel varieties. The conflicts caused by useful-noxious invasive species point to the need of coordination and cooperation among government agencies and to the research needed to provide alternatives to the people that depend on those invasive species.

Regarding the ecological research on invasive species, the environments that they invade and the plant invasion processes, these research topics in Mexico are still limited, disarticulated and clearly insufficient for the challenges posed by a mega-diverse country as Mexico. With the exception of the marsh invaded by E. pyramidalis , there are few continued efforts to study and restore environments invaded by invasive weeds. Taken as a group, the restoration studies involving invasive weeds are also disarticulated and performed by very few specialized researchers in restoration ecology.

The largest set of publications reviewed here is concerned with invasive management, mainly about biological control concentrated in few high-impact invasive species such as E. crassipes, S. halepense or C. arvensis . Unfortunately most management studies concentrate in one invasive weed and one control agent. The problems posed by non-native species are complex and varied, but they cannot and should not be treated with an approach exclusively focused on an invasive species. Instead, an ecosystemic approach should be used to prevent and treat biological invasions. For example, a review of Australian ecosystem responses to invasive weed removal, indicated that in most cases recolonization of the sites with other weeds, native or non-native, was observed and in few cases plant recolonization was conductive to the local ecosystem restoration ( Reid, Morin, Downey, French, & Virtue, 2009 ).

The scientific knowledge generated by Mexican researchers for plant invasions in Mexico is not enough, although most of it is of high quality, and the goals concerning scientific knowledge set for 2020 in the National Strategy on Invasive species probably will not be met.

A valid question can be raised on the need for developing scientific information on invasives and plant invasions in Mexico when thousands of papers on these topics are available in the international scientific literature. Unfortunately, although much of the international literature is useful to understand general patterns and process in biological invasions, the state of the art on understanding invasions is not well integrated ( Jeschke, 2014 ). Moreover, a recent review on the scientific support for the main hypotheses that try to explain the nature of invasive species, the invaded ecosystems and the interactions between invaders and ecosystems, found incomplete support, and in many cases evidence that does not support or contradict those hypothesis ( Moles et al., 2012 ). The reasons offered for the incomplete support or contradictory evidence, are the idiosyncratic nature of each invasive species and the invaded environments. This means that the experimental results vary depending on the taxonomic and/or ecological group to which invasive species belong. Also, results on ecosystem invasibility or ecosystemic impacts are also idiosyncratic, change with time and depend on the history of the invasion and the invaded ecosystem ( Kueffer et al., 2013; Moles et al., 2012 ). To face the idiosyncratic and dynamic nature of invasive species, invaded ecosystems and the interactions between them, integrated studies with selected model species and model ecosystems repeated around the world have been proposed, as well as meta-analysis of the thousands of papers on invasives and invasions ( Kueffer et al., 2013).

The Mexican research on non-native weeds and invasions has made some contributions to the management and policy on invasive plants and invasions, but most of the management has been empirically based, reproducing the empirical management mostly developed in the first world. For example, the widely accepted scheme of early detection and eradication of invasive weeds and the cost associated to this scheme has been developed in Australia and the United States ( Mendoza et al., 2009; Panetta, 2015; Rejmánek & Pitcairn, 2002 ). Risk analysis in Mexico for unwanted weeds is based mainly in the Australian scheme ( Panetta, 1993; Pheloung, Williams, & Halloy, 1999 ), which has been adapted for other countries such as the United States ( Gordon, Tancig, Onderdonk, & Gantz, 2011 ). A preliminary effort to contribute to risk analysis for non-native species already present species in Mexico was developed for Fabaceae ( s.l.) species (Sánchez-Blanco et al., 2012).

Perspectives on invasive weed research

Given the incomplete knowledge of plant invasions and their idiosyncratic and dynamic nature, invasive weed management in Mexico should continue adjusting the empirical knowledge generated abroad and devising new empirical approaches derived from the scientific knowledge developed specifically for Mexican ecosystems affected by invasions. For example, among the many areas in which Mexican and International research can be integrated is that of determination of vulnerability to invasions. A map predicting the vulnerability to invasions for Mexico was obtained overlapping maps with propagule availability, vegetation type, anthropic disturbance and native plant species richness ( del Val et al., 2015 ); the correlation of the four variables with non-native plant incidence was obtained previously by international researchers, and the confirmation of the correlations was obtained for Mexico ( Espinosa-García et al., 2004b ). A further improvement of this model can be obtained by indicating which vulnerable regions are prone to be invaded by weeds imported from different parts of the world in a similar way as the work done for India by modeling susceptibility of its regions to weeds from North America, South America, Europe, Africa and Australia ( Adhikari, Tiwary, & Barik, 2015 ). The improved model would be very useful for prevention and surveillance in early detection programs.

The publications included in this review are of high quality showing that Mexico has an important, but not sufficient, number of researchers able to generate the scientific knowledge important for the prevention and management of the non- native weeds. However, the prevalent pattern of the Mexican research on non-native weeds for all research topics reflects research produced by few academic groups, but mostly disarticulated and few times connected with decision makers. Thus, a primary task to meet the scientific knowledge needs to prevent and/or manage biological invasions in Mexico is to engage young researchers on invasions and coordinate them with the existent researchers to investigate a highly selected series of topics identified in the National Strategy for Biological Invasions (see Espinosa-García, 2009; Espinosa-García et al., 2009 ). This can be achieved opening new academic positions in universities and research institutions and through competitive research funds administrated by the National Commission on the Knowledge and use of Biodiversity (Conabio) or the National Commission of Science and Technology (Conacyt).

Another key task is capacity building at all levels, from the general public to recognize and report invasive species, to postgraduate students specializing in invasive species and biological invasions. The existing and future Mexican researchers should integrate also with international researchers to study model invaded ecosystems and model invasive species to advance the theory on biological invasions.

Final observations

Summarizing, the last few years we had made considerable advances collecting basic information on non-native weeds. Introduced species’ impact in Mexico is perhaps lower than that in countries that are our main trade partners. However, there are species such as water lily and several African grasses, which cause considerable damage to agricultural and natural landscapes. An urgent task is a full assessment of the actual and potential impact of non-native species on Mexican ecosystems to prioritize the weeds and regions that require immediate attention. Of course, this task cannot be completed without a previous full knowledge of the identity, abundance and distribution of the weeds introduced in Mexico.

Acknowledgements

The authors thank Miguel Martínez Ramos for the invitation to elaborate this review. We also thank Yolanda M. García Rodríguez for help in the references formatting and to Heberto Ferreira and Alberto Valencia for their help with databases and computing. We acknowledge the corrections and comments from two anonymous reviewers of an earlier version of this manuscript. This work was supported by IIES-UNAM-POFJEG.

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